Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification...

60
Environment Protection Authority Lower Murray Reclaimed Irrigation Area (LMRIA) Acidification Project Final monitoring report 2013

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Environment Protection Authority

Lower Murray Reclaimed Irrigation Area (LMRIA) Acidification Project

Final monitoring report 2013

Lower Murray Reclaimed Irrigation Area (LMRIA) Acidification Project Final monitoring report 2013

This project is a joint project between the MurrayndashDarling Basin Authority and the South Australia Government

Authors Peter Mettam Luke Mosley David Palmer Peter Scott Benjamin Zammit Emily Leyden and Courtney Cummings

For further information please contact

Information Officer Environment Protection Authority GPO Box 2607 Adelaide SA 5001

Telephone (08) 8204 2004 Facsimile (08) 8124 4670 Free call (country) 1800 623 445

Website ltwwwepasagovaugt

Email ltepainfoepasagovaugt

ISBN 978-1-921495-52-6

July 2014

copy Environment Protection Authority

This document may be reproduced in whole or part for the purpose of study or training subject to the inclusion of an acknowledgment of the source and to it not being used for commercial purposes or sale Reproduction for purposes other than those given above requires the prior written permission of the Environment Protection Authority

Contents Abbreviations 6

Acknowledgments7

Summary 8

1 Introduction 9

2 Results 18

3 Discussion56

4 Conclusion 58

5 Recommendations59

6 References60

List of figures Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought) 100

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 201211

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) 12

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA 14

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment15

Figure 6 Sediment trap positioning15

Figure 7 Benthic sediment sampling locations 16

Figure 8 Salt drain pH for drains south of Murray Bridge 18

Figure 9 Salt drain pH for drains North of Murray Bridge 19

Figure 10 Acidity concentrations for salt drains south of Murray Bridge19

Figure 11 Acidity concentrations for salt drains North of Murray Bridge20

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge 21

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge21

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge22

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge 22

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Bridge24

Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge 24

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge 24

Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge24

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge 25

Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge25

Figure 22 Total manganese concentrations for LMRIA salt drains south of Murray Bridge 25

Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Bridge 25

Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge 26

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge26

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 26

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 26

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge27

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 27

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge30

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge 30

Figure 34 Discharge of acid drainage water into the River Murray31

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011 32

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 201333

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 201334

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013 35

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 36

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows38

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows 39

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 40

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at Jervois52

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington53

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 201355

List of tables Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water 28

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water29

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain 42

Table 4 Localised plume summary statistics ndash inside immediate mixing zone 45

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone 48

Table 6 Total recoverable metals in sediment and precipitates within JervoisndashWellington drain and plume area51

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area 51

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 201354

Abbreviations ANZECC Australian and New Zealand Environment Conservation Council

ASS acid sulfate soils

EPA South Australian Environment Protection Authority

LMRIA Lower Murray Reclaimed Irrigation Area

MDBA MurrayndashDarling Basin Authority

6

Acknowledgments The cooperation and assistance of various irrigators and irrigation trusts across the LMRIA are greatly appreciated

In particular we would like to thank Barry and Joanne Pfeiffer at Long Flat for the use of their farm as an acid drainage management trial site and assistance with various aspects of the project

We would like to thank Drs Rob Fitzpatrick Paul Shand and Andrew Baker from CSIRO for contributing to the scientific understanding of the issue

We would also like to thank Dr Freeman Cook (Freeman Cook and Associates Pty Ltd) for assistance and advice on groundwater hydrological processes and calculations at Long Flat The assistance of Rob Frazer in the installation of piezometers is also gratefully acknowledged

Thank you to Hon Dean Brown and the Lower Murray Sustainable Soils Reference Group for useful discussions and support for the project The advice of Martin Philcox and Monique White is particularly acknowledged

This project was funded by the Environment Protection Authority (EPA) Government of South Australia (under the Save the River Murray Fund) Primary Industries and Resources South Australia (PIRSA) and the MurrayndashDarling Basin Authority (MDBA)

Special mention must go to Rob Kingham from the MDBA who has offered robust support for both the science and management of the acid sulfate soils issue in the LMRIA region

7

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

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LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

040

080

120

Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

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4

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6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
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                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 2: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

Lower Murray Reclaimed Irrigation Area (LMRIA) Acidification Project Final monitoring report 2013

This project is a joint project between the MurrayndashDarling Basin Authority and the South Australia Government

Authors Peter Mettam Luke Mosley David Palmer Peter Scott Benjamin Zammit Emily Leyden and Courtney Cummings

For further information please contact

Information Officer Environment Protection Authority GPO Box 2607 Adelaide SA 5001

Telephone (08) 8204 2004 Facsimile (08) 8124 4670 Free call (country) 1800 623 445

Website ltwwwepasagovaugt

Email ltepainfoepasagovaugt

ISBN 978-1-921495-52-6

July 2014

copy Environment Protection Authority

This document may be reproduced in whole or part for the purpose of study or training subject to the inclusion of an acknowledgment of the source and to it not being used for commercial purposes or sale Reproduction for purposes other than those given above requires the prior written permission of the Environment Protection Authority

Contents Abbreviations 6

Acknowledgments7

Summary 8

1 Introduction 9

2 Results 18

3 Discussion56

4 Conclusion 58

5 Recommendations59

6 References60

List of figures Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought) 100

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 201211

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) 12

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA 14

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment15

Figure 6 Sediment trap positioning15

Figure 7 Benthic sediment sampling locations 16

Figure 8 Salt drain pH for drains south of Murray Bridge 18

Figure 9 Salt drain pH for drains North of Murray Bridge 19

Figure 10 Acidity concentrations for salt drains south of Murray Bridge19

Figure 11 Acidity concentrations for salt drains North of Murray Bridge20

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge 21

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge21

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge22

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge 22

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Bridge24

Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge 24

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge 24

Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge24

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge 25

Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge25

Figure 22 Total manganese concentrations for LMRIA salt drains south of Murray Bridge 25

Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Bridge 25

Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge 26

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge26

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 26

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 26

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge27

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 27

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge30

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge 30

Figure 34 Discharge of acid drainage water into the River Murray31

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011 32

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 201333

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 201334

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013 35

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 36

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows38

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows 39

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 40

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at Jervois52

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington53

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 201355

List of tables Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water 28

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water29

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain 42

Table 4 Localised plume summary statistics ndash inside immediate mixing zone 45

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone 48

Table 6 Total recoverable metals in sediment and precipitates within JervoisndashWellington drain and plume area51

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area 51

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 201354

Abbreviations ANZECC Australian and New Zealand Environment Conservation Council

ASS acid sulfate soils

EPA South Australian Environment Protection Authority

LMRIA Lower Murray Reclaimed Irrigation Area

MDBA MurrayndashDarling Basin Authority

6

Acknowledgments The cooperation and assistance of various irrigators and irrigation trusts across the LMRIA are greatly appreciated

In particular we would like to thank Barry and Joanne Pfeiffer at Long Flat for the use of their farm as an acid drainage management trial site and assistance with various aspects of the project

We would like to thank Drs Rob Fitzpatrick Paul Shand and Andrew Baker from CSIRO for contributing to the scientific understanding of the issue

We would also like to thank Dr Freeman Cook (Freeman Cook and Associates Pty Ltd) for assistance and advice on groundwater hydrological processes and calculations at Long Flat The assistance of Rob Frazer in the installation of piezometers is also gratefully acknowledged

Thank you to Hon Dean Brown and the Lower Murray Sustainable Soils Reference Group for useful discussions and support for the project The advice of Martin Philcox and Monique White is particularly acknowledged

This project was funded by the Environment Protection Authority (EPA) Government of South Australia (under the Save the River Murray Fund) Primary Industries and Resources South Australia (PIRSA) and the MurrayndashDarling Basin Authority (MDBA)

Special mention must go to Rob Kingham from the MDBA who has offered robust support for both the science and management of the acid sulfate soils issue in the LMRIA region

7

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

10

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

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120

Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

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8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

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9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

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800

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

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400

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600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

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8000

10000

12000

14000

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16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

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15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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ium

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L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Alu

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ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

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03

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

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Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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tal A

lum

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m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
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                                    • ColumnTitle_2
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Page 3: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

Contents Abbreviations 6

Acknowledgments7

Summary 8

1 Introduction 9

2 Results 18

3 Discussion56

4 Conclusion 58

5 Recommendations59

6 References60

List of figures Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought) 100

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 201211

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) 12

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA 14

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment15

Figure 6 Sediment trap positioning15

Figure 7 Benthic sediment sampling locations 16

Figure 8 Salt drain pH for drains south of Murray Bridge 18

Figure 9 Salt drain pH for drains North of Murray Bridge 19

Figure 10 Acidity concentrations for salt drains south of Murray Bridge19

Figure 11 Acidity concentrations for salt drains North of Murray Bridge20

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge 21

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge21

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge22

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge 22

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Bridge24

Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge 24

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge 24

Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge24

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge 25

Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge25

Figure 22 Total manganese concentrations for LMRIA salt drains south of Murray Bridge 25

Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Bridge 25

Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge 26

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge26

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 26

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 26

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge27

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 27

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge30

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge 30

Figure 34 Discharge of acid drainage water into the River Murray31

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011 32

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 201333

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 201334

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013 35

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 36

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows38

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows 39

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 40

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at Jervois52

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington53

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 201355

List of tables Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water 28

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water29

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain 42

Table 4 Localised plume summary statistics ndash inside immediate mixing zone 45

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone 48

Table 6 Total recoverable metals in sediment and precipitates within JervoisndashWellington drain and plume area51

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area 51

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 201354

Abbreviations ANZECC Australian and New Zealand Environment Conservation Council

ASS acid sulfate soils

EPA South Australian Environment Protection Authority

LMRIA Lower Murray Reclaimed Irrigation Area

MDBA MurrayndashDarling Basin Authority

6

Acknowledgments The cooperation and assistance of various irrigators and irrigation trusts across the LMRIA are greatly appreciated

In particular we would like to thank Barry and Joanne Pfeiffer at Long Flat for the use of their farm as an acid drainage management trial site and assistance with various aspects of the project

We would like to thank Drs Rob Fitzpatrick Paul Shand and Andrew Baker from CSIRO for contributing to the scientific understanding of the issue

We would also like to thank Dr Freeman Cook (Freeman Cook and Associates Pty Ltd) for assistance and advice on groundwater hydrological processes and calculations at Long Flat The assistance of Rob Frazer in the installation of piezometers is also gratefully acknowledged

Thank you to Hon Dean Brown and the Lower Murray Sustainable Soils Reference Group for useful discussions and support for the project The advice of Martin Philcox and Monique White is particularly acknowledged

This project was funded by the Environment Protection Authority (EPA) Government of South Australia (under the Save the River Murray Fund) Primary Industries and Resources South Australia (PIRSA) and the MurrayndashDarling Basin Authority (MDBA)

Special mention must go to Rob Kingham from the MDBA who has offered robust support for both the science and management of the acid sulfate soils issue in the LMRIA region

7

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

10

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

040

080

120

Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

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50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 4: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge 27

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge 27

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge30

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge 30

Figure 34 Discharge of acid drainage water into the River Murray31

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011 32

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 201333

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 201334

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013 35

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 36

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows38

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows 39

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows 40

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at Jervois52

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington53

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 201355

List of tables Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water 28

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water29

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain 42

Table 4 Localised plume summary statistics ndash inside immediate mixing zone 45

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone 48

Table 6 Total recoverable metals in sediment and precipitates within JervoisndashWellington drain and plume area51

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area 51

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 201354

Abbreviations ANZECC Australian and New Zealand Environment Conservation Council

ASS acid sulfate soils

EPA South Australian Environment Protection Authority

LMRIA Lower Murray Reclaimed Irrigation Area

MDBA MurrayndashDarling Basin Authority

6

Acknowledgments The cooperation and assistance of various irrigators and irrigation trusts across the LMRIA are greatly appreciated

In particular we would like to thank Barry and Joanne Pfeiffer at Long Flat for the use of their farm as an acid drainage management trial site and assistance with various aspects of the project

We would like to thank Drs Rob Fitzpatrick Paul Shand and Andrew Baker from CSIRO for contributing to the scientific understanding of the issue

We would also like to thank Dr Freeman Cook (Freeman Cook and Associates Pty Ltd) for assistance and advice on groundwater hydrological processes and calculations at Long Flat The assistance of Rob Frazer in the installation of piezometers is also gratefully acknowledged

Thank you to Hon Dean Brown and the Lower Murray Sustainable Soils Reference Group for useful discussions and support for the project The advice of Martin Philcox and Monique White is particularly acknowledged

This project was funded by the Environment Protection Authority (EPA) Government of South Australia (under the Save the River Murray Fund) Primary Industries and Resources South Australia (PIRSA) and the MurrayndashDarling Basin Authority (MDBA)

Special mention must go to Rob Kingham from the MDBA who has offered robust support for both the science and management of the acid sulfate soils issue in the LMRIA region

7

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

10

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

040

080

120

Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 5: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

Abbreviations ANZECC Australian and New Zealand Environment Conservation Council

ASS acid sulfate soils

EPA South Australian Environment Protection Authority

LMRIA Lower Murray Reclaimed Irrigation Area

MDBA MurrayndashDarling Basin Authority

6

Acknowledgments The cooperation and assistance of various irrigators and irrigation trusts across the LMRIA are greatly appreciated

In particular we would like to thank Barry and Joanne Pfeiffer at Long Flat for the use of their farm as an acid drainage management trial site and assistance with various aspects of the project

We would like to thank Drs Rob Fitzpatrick Paul Shand and Andrew Baker from CSIRO for contributing to the scientific understanding of the issue

We would also like to thank Dr Freeman Cook (Freeman Cook and Associates Pty Ltd) for assistance and advice on groundwater hydrological processes and calculations at Long Flat The assistance of Rob Frazer in the installation of piezometers is also gratefully acknowledged

Thank you to Hon Dean Brown and the Lower Murray Sustainable Soils Reference Group for useful discussions and support for the project The advice of Martin Philcox and Monique White is particularly acknowledged

This project was funded by the Environment Protection Authority (EPA) Government of South Australia (under the Save the River Murray Fund) Primary Industries and Resources South Australia (PIRSA) and the MurrayndashDarling Basin Authority (MDBA)

Special mention must go to Rob Kingham from the MDBA who has offered robust support for both the science and management of the acid sulfate soils issue in the LMRIA region

7

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

10

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

040

080

120

Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

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4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

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Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

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6000

8000

10000

12000

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16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

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20000

25000

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Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

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ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Alu

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ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

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0025

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0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

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tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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n (m

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Long Flat Pompoota Burdett Toora Mobilong

320

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20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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5

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15

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25

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35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

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15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

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6

8

10

12

14

16

18

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

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40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 6: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

Acknowledgments The cooperation and assistance of various irrigators and irrigation trusts across the LMRIA are greatly appreciated

In particular we would like to thank Barry and Joanne Pfeiffer at Long Flat for the use of their farm as an acid drainage management trial site and assistance with various aspects of the project

We would like to thank Drs Rob Fitzpatrick Paul Shand and Andrew Baker from CSIRO for contributing to the scientific understanding of the issue

We would also like to thank Dr Freeman Cook (Freeman Cook and Associates Pty Ltd) for assistance and advice on groundwater hydrological processes and calculations at Long Flat The assistance of Rob Frazer in the installation of piezometers is also gratefully acknowledged

Thank you to Hon Dean Brown and the Lower Murray Sustainable Soils Reference Group for useful discussions and support for the project The advice of Martin Philcox and Monique White is particularly acknowledged

This project was funded by the Environment Protection Authority (EPA) Government of South Australia (under the Save the River Murray Fund) Primary Industries and Resources South Australia (PIRSA) and the MurrayndashDarling Basin Authority (MDBA)

Special mention must go to Rob Kingham from the MDBA who has offered robust support for both the science and management of the acid sulfate soils issue in the LMRIA region

7

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

10

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

040

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120

Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

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8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

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9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

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600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

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8000

10000

12000

14000

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20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

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10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Alu

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ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Alu

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ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Ars

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L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

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0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

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tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

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02

03

04

05

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

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1

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 7: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

Summary Due to very low inflows from the MurrayndashDarling Basin from 2007ndash10 water levels in the Lower Murray River (below Lock 1) fell from a normal pool level of +075 m AHD to a low of ndash12 m AHD The low water levels and restricted water allocations for irrigation during this hydrological drought meant that most of the Lower Murray Reclaimed Irrigation Area (LMRIA) on the historic floodplain of the river was not irrigated The low river levels and lack of irrigation led to a drop in the shallow water table of 15ndash3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the irrigation bays and associated infrastructure and major socio-economic impacts

Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 salt drains across 13 of the 27 LMRIA irrigation areas Investigations by the EPA and CSIRO determined that the falling groundwater levels under the LMRIA from 2007ndash09 led to the exposure and oxidation of reduced inorganic sulfur minerals commonly termed acid sulfate soils The acid and metals which were produced in the soil profile as a result of the oxidation process were then mixed with the shallow groundwater as water levels recovered in the Lower Murray in late 2010 This resulted in acidic drainage water entering the LMRIA salt drains As a necessary process to keep the saline water tables below pasture in this agricultural region the acidic drainage water is pumped back into the River Murray

In response to these findings and the potential risks that acidic drainage water poses to the water quality and environmental values of the Lower River Murray a monitoring and assessment project was initiated This project included three main monitoring components

bull assessment of drainage water quality and volumes across the LMRIA

bull assessment of the drainage plume water quality and behaviour following discharge to the River Murray

bull assessment of heavy metal precipitates discharged with drainage water and their affect on benthic ecology

Results have demonstrated low pH and acidic conditions persist in the salt drains despite an end to the drought and regular irrigation events High dissolved metal levels that exceed water quality protection guidelines also still persevere in many salt drains

Despite the poor water quality within the salt drains monitoring of discharge events has illustrated that the acidic drainage water is quickly neutralised as it enters the river channel Monitoring of the mixing of the acid drainage plumes within the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During lower river flow conditions the plumes extend further downstream and were also identified as flowing upstream at several sites in 2013 By the time the acid drainage water reaches the main river channel only minor andor occasional exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges consistent with the acid sulfate soil sources

During the high flow conditions of late 2010 to January 2013 monitoring of salt drain discharges into the River did not identify a significant risk to public water supplies or river users Monitoring has continued during the recent period of decreasing flows However as yet no new risk to human health has been identified

Sediment sampling at the JervoisndashWellington acidic drain and discharge point has identified high concentrations of metal precipitates such as iron aluminium and manganese well in excess of ANZECC guidelines Sediment within the salt drain reported very high metal concentrations including iron concentrations at 20 of total sediments sampled

Benthic sampling undertaken at the JervoisndashWellington acidic drain suggests that there is significant difference between shallow bank ecology and river channel ecology but no significant variability between benthic ecology upstream and downstream of the discharge point Predominant species are those with a high tolerance to poor water conditions

It is recommended that monitoring of salt drains and discharge events continues in order to improve the understanding of how the concentration of acidity and associated metals varies over differing temporal and spatial scales Future monitoring will also assist in the evaluation of the various remediation trials undertaken over an extended period

8

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

9

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

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LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

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m(A

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Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

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LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

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LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

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pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

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pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

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Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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linity

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o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

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Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

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(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

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LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

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LMRIA Salt Drain Total Arsenic- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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LMRIA Salt Drain Total Nickel- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

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e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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Page 8: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

1 Introduction The Lower Murray Reclaimed Irrigation Area (LMRIA) includes approximately 5200 hectares of flood irrigated agriculture between the townships of Mannum and Wellington The 27 individual irrigation areas that make up the LMRIA were created on the former floodplains of the River Murray in South Australia and were drained and developed for agriculture between 1880 and 1940 Historically the predominant land use was dairy farming with a smaller area used for beef cattle fodder production and lifestyle farming

In the past agriculture in this area was inefficient in water use and the irrigation practices returned large volumes of polluted water with high levels of salt nutrients and pathogens to the River Murray (Mosley amp Fleming 2009) As a result of the risk to environmental values (drinking water recreation aquatic ecosystems) within the lower MurrayndashDarling Basin the state government worked with irrigators on a $22-million Commonwealth funded project from 2003ndash06 to improve water and land management practices in the LMRIA

Key outcomes from the rehabilitation project were the installation of efficient irrigation and runoff reuse systems to reduce the pollutant loads returned to the river and improved on-farm management practises (EPA 2009) In particular the project focused on infrastructure improvements such as new water delivery infrastructure (siphonssluices inlet channels) water metering laser grading of paddock surfaces and construction of runoff reuse systems (gt50 kLha capacity) to recycle excess surface irrigation runoff water and pollutants (that were previously returned to the river) back onto the farm

During April 2009 the water level in the Lower Murray fell to below ndash1m AHD the lowest river level since records began The low water levels restricted irrigation water allocations during the drought meant that most of the reclaimed areas were not able to be irrigated for substantial periods of time which led to a drop in the water table of up to 3 m from pre-drought levels The heavy clay soils subsequently salinised dried and cracked causing major damage to the rehabilitated irrigation bays and associated infrastructure Screening by the EPA in late February 2011 highlighted the presence of acid water in 14 LMRIA salt drains at 13 irrigation areas comprising a total area of approximately 3500 ha

In response to these findings a monitoring project was undertaken to examine the nature and risks of acid drainage originating from the LMRIA to the Lower River Murray water quality This monitoring work complements other activities being undertaken through a broader LMRIA project with the MurrayndashDarling Basin Authority (MDBA) to assess the risks to Lower Murray water quality and aquatic ecosystems from acid drainage discharges The outcomes of this project will also assist in the development of management options to both protect the environmental values in the River Murray and farm productivity in the region

A previous report (EPA 2012) detailed the results of monitoring from 2011ndash12 This final report contains updated results and analysis to June 2013 on monitoring of acid drainage in the LMRIA and associated discharge zones in the River Murray New results on sediment and benthic ecosystem analysis are also included

11 Description of the Lower Murray Reclaimed Irrigation Area

111 Regional hydro-geological setting

The Murray River Basin in South Australia which includes LMRIA at its southern end overlies a basement rock and consists of layers of limestone sands and clays up to 150 m thick The main regional aquifer is the Murray Group Limestone which is about 25ndash30 m thick Below this aquifer is the Remark Group aquifer (inter-bedded sands and lignite clays) which are around 10ndash30 m thick It is confined from the Murray Group Limestone aquifer by the Ettrick Formation a grey-green fossiliferous marl

Regional groundwater flows through pore spaces in the limestone beds towards the River Murray Valley and alluvial floodplains which are the point of discharge (Barnett 1989) The sediments of the valley were deposited during a period of rapid sea level rise which followed an ice age 20000 years ago The medium to coarse grain sands of the Monoman Formation (5ndash20 m thick) are overlaid by the finer mostly alluvial clays silts and sands of the Coonambidgal Formation (10ndash20 m thick)

The sediments of the Monoman Formation form a permeable aquifer (connected to the lower limestone aquifer) which is semi-confined by the upper Coonambidgal Formation The regional groundwater flows beneath the floodplain in the

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LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

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LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

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Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

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LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

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LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

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LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

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LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

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LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

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LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

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LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

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pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

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Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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as C

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

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LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

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(mg

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

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Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

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(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

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Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

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LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

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LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

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LMRIA Salt Drain Total Arsenic- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

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LMRIA Salt Drain Total Nickel- North of Murray Bridge

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L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
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Page 9: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

alluvial sediments of the Monoman and Coonambidgal Formations to its discharge point which was originally the River Murray (Barnett 1989)

From the 1920s to 1940s a series of large infrastructure projects were initiated along the River Murray This included the construction of locks and barrages and levee banks along the river channel Before these changes were initiated the hydrological regime in the area was variable with the river level rising and falling with seasonal fluctuations Due to the connectivity to the river the water table below the floodplain also fluctuated over the seasons The regional groundwater discharge point would have been the River Murray owing to it being the lowest point in the landscape

Once the locks and barrages were built however the river was maintained at a relatively constant level eliminating large seasonal fluctuations This along with the construction of the levee banks which contained and raised the level of the river in the main channel benefited the development of agriculture on the reclaimed swamps as it ensured water security and enabled low-cost gravity fed irrigation

However the infrastructure changes also altered the hydrological regime of the area with the swamps becoming the new discharge point for the highly saline (10000 to 15000 EC units) regional groundwater To prevent the land from becoming salinised a series of drainage channels were installed to intercept the regional groundwater to form a new point of discharge and was flood irrigated regularly during summer (Figure 1) The drainage channels and irrigation were able to keep the local water table in the swamps around 1 m below the surface

112 Irrigation areas

The LMRIA is separated into 27 irrigation areas 24 of which were actively farmed (predominantly dairy agriculture) prior to the drought in 2007 The conceptual diagram (Figure 1) illustrates a typical flood irrigation area in the LMRIA Irrigation areas are constructed to have a lower elevation than the river so that water can be gravity fed through sluice gates and siphons in the levee banks onto each irrigation bay The runoff and sub-surface drainage then collects in the lateral side drains and the back channel known as the lsquosalt drainrsquo or lsquomain drainrsquo and this is subsequently pumped back into the River Murray or recycled onto other areas through reuse pumps The salt drains also receive regional and local irrigation groundwater inputs and occasional stormwater runoff from adjacent highland areas including townships in some locations

Figure 1 Conceptual diagram of a typical flood irrigation area in the LMRIA (pre-drought)

During the prolonged hydrological drought from 2006ndash10 many of the enterprises in the LMRIA ceased operation due to inability to irrigate (low river water levels) and irrigation water allocation restrictions The remaining commercially operating farms have reported significantly reduced productivity when compared to pre-drought conditions and approximately 1008 ha of LMRIA farmland is currently classified as unproductive (Philcox and Scown 2012) In many cases agriculture on the LMRIA irrigation areas has moved towards mainly beef and fodder production although a reduced number of dairies are still operational

10

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

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Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

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LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

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Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

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pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

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as C

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

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Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

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Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

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Elec

trica

l Con

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ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

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Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

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LMRIA Salt Drain Total Arsenic- North of Murray Bridge

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Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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LMRIA Salt Drain Total Manganese- North of Murray Bridge

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Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

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LMRIA Salt Drain Total Nickel- North of Murray Bridge

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Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

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Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

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LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

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LMRIA Salt Drain Soluble Iron- North of Murray Bridge

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Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 10: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

113 Acid sulfate soils in the LMRIA

The artificially stable and more saturated water conditions in the Lower Murray region over the last century coupled with the availability of sufficient iron sulfate and organic material have allowed the build-up of pyrite (FeS2) in the LMRIA soils (below the water table 1ndash3 m below ground level) The pyrite containing soils commonly known as acid sulfate soils (ASS) in the LMRIA did not pose a problem under saturated and anaerobic conditions

During the drought the River Murray level below Lock 1 dropped from the long-term average pool level of +07 m AHD to ndash1 m AHD and subsequently the groundwater level underneath the irrigation areas dropped up to 3 m (Figure 2) This allowed the soils to dry and form large cracks (up to 2 m in depth) in the largely clay profile The drying and cracking of the clay soils introduced oxygen to the profile for the first time in 100 years which reacted with the pyrite present to produce sulfuric materials (pHlt4 see conceptual model in Fig 3) The zone of formation of sulfuric materials corresponds to the depth of decline of the water table during the drought This process also mobilises dissolved metals such as aluminium iron arsenic and manganese from the soil profile (Simpson et al 2010) The top metre of the clay soils was likely prevented from forming significant ASS due to the regular wetting and drying cycles associated with flood irrigation over the last 100 years Upstream flooding in late 2009 and 2010 led to the River Murrayrsquos water levels returning to historical average levels

The data available from the pre- and post-drought of both the River Murray water levels and the groundwater levels in the irrigation areas (Figure 2) suggest that there was a critical water level in the River Murray (~ 05 m AHD) which is required to prevent the groundwater in the irrigation areas from falling to levels where pyrite is oxidised The connectivity between the River Murray water level and the groundwater in the LMRIA warrants further research to better understand the hydrological processes involved

Mobilong and Mypolonga Groundwater Levels 2003 - 2012

Below 05 mAHD in river groundwater

-360

-320

-280

-240

-200

-160

-120

-080

-040

000

040

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Sep-02 Oct-03 Nov-04 Dec-05 Jan-07 Feb-08 Mar-09 May-10 Jun-11 Jul-12

m(A

HD)

Mobilong 1A (5m) Mypolonga MOB029 (8m) Murray Bridge Water Level 05 m AHD

Groundwater has fallen gt12 m on Mobilong Swamp and 3m on Mypolonga Swamp from pre drought levelSignificant quanities of pyrite are oxisided soil and water acidication occurrs acid drainage returned to the River Murray when river levels return

level has declined 05-12 m (note lag time in groundwater response)

Figure 2 Groundwater level at Mobilong and Mypolonga from 2002 to 2012 This graph clearly illustrates that the groundwater level in the irrigation areas begins to drop disproportionately once the water level in the River Murray drops below 05 m AHD

River water levels recovered in the Lower Murray in late 2010 (Fig 2) The subsequent rise in the groundwater table under the LMRIA led to a mixing of groundwater back up through the acidic soil profile Due to the rising water table irrigation or large rainfall events this acidic groundwater is transported and collected in side and salt drains of the irrigation areas Once collected in the salt drain this acidic water must be pumped back into the River Murray to prevent back flooding of pastures and major damage to agricultural values The return of acid drainage water to the River Murray presented a potential risk to River Murray water quality and its environmental values

11

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

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9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

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16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

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Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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gL

as C

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Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

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07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

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Elec

trica

l Con

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ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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rsen

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gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Man

gane

se (m

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Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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kel (

mg

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Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

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14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

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14

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

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45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

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m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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Page 11: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Figure 3 Conceptual diagram of the process of acid sulfate soil oxidation in the LMRIA (from CSIRO 2013) Lowering of the water table during the 2008ndash10 drought exposed acid sulfate soils that subsequently oxidised releasing sulfuric material As the water table recovers post-drought the sulfuric material mixes with the rising waters and is flushed into the LMRIA salt drains

12

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
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Page 12: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

12 Sampling programs The LMRIA Acidification Risk Project consists of three sampling programs

1 Sampling of both acidic and neutral salt drains across the LMRIA

2 Plume monitoring in the River Murray downstream of key acidic drainage water discharge points

3 Sediment and benthic ecology sampling within the JervoisndashWellington salt drain and at its discharge point

121 Salt drain sampling

There are 27 salt drains in the LMRIA region (Figure 4) Following initial screening in March 2011 14 of these salt drains (from 13 irrigation areas) were found to be acidic The acidic salt drains were sampled on a fortnightly basis whilst the neutral salt drains were monitored on an occasional basis Sampling was undertaken at the pump shed as this is the point directly before the water is pumped back into the River Murray Eight of the largest acidic salt drains in the LMRIA have loggers installed at the pump shed which record the daily pumping volumes to the River Murray This data was used in combination with field data to estimate acidity loads to the River Murray from those acidic drains

122 Plume sampling

Plume sampling was conducted in the river adjacent to salt drain pump sheds during discharge events Sampling of plumes would on average be undertaken after two hours of pumping in order to allow the discharge plume to establish Transects were conducted from the point of discharge out into the channel and continued downstream and upstream until the extent of the plume was determined Water quality parameters were recorded using a 6820 Sonde water quality meter at 1 m intervals at each monitoring point to create depth profiles within the river Samples for laboratory analysis were collected at three depths including the surface the mid-point and the bottom of a vertical depth transect using a Van Dorne Water Sampler Sampling was also conducted at a reference site upstream of the discharge point

13

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
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Page 13: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Figure 4 Location of discharge points and status (neutral or acidic) of salt drain water quality in August 2012 for the 27 irrigation areas in the LMRIA The drinking water offtakes and townships (Mannum Murray Bridge Tailem Bend and Wellington) are also shown in the region

14

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

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450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
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Page 14: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

123 Sediment and precipitates sampling

Sampling of sediment within the river and precipitates falling out of suspension during pumping events was undertaken at the Jervois (Wellington end) salt drain discharge zone Two sediment traps (Figure 5) were placed along a buoy line approximately 3 m from the discharge point and left in situ for a fortnight (Figure 6) Another two sediment traps were placed in the salt drain for comparison

The sediment trap is a PVC cylinder (500 mm high x 150 mm deep) open at the top with a sealed lsquosediment catchrsquo at the bottom Within the main cylinder are several smaller PVC tubes to reduce the likelihood of non-sediment debris (eg twigs large rocks) entering the sediment trap At the end of the two-week sampling period the sediment traps were retrieved and all sedimentprecipitates were placed in sterile glass jars and stored in accordance with NATA accredited laboratory requirements

Sediment grab samples were collected at Jervois (Wellington end) using a Wildco sediment grab Six samples were collected (approximately 500 g of wet sediment per sample) including three channel and two shallow bank samples as well as a sample taken 3 m from the discharge point (near the buoy line sediment trap) An additional sample was taken directly from the salt drain was also collected for comparison The Wildco Sediment grab was lowered to the sediment surface and activated to collect a fragment of riverbed sediment When retrieved the sample was placed in a sterile glass jar and stored in accordance with NATA accredited laboratory requirements

Figure 5 This sediment trap is the 50-cm drain version retrieved and sampled after two weeks of deployment The staining on the exterior is most likely a result of iron-based bacteria

Figure 6 Sediment trap positioningsediment trap sits upright on the river bed for a two-week period collecting sediment and metal precipitates as they fall out of suspension

15

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

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5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

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Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

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8000

10000

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16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

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20000

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Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Alu

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ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

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l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

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001

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0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

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tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

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170

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20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

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15

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

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20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

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6

8

10

12

14

16

18

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

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Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

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6

8

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12

14

16

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

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10

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

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10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
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Page 15: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

124 Benthic ecology sampling

Six sampling locations were used at JervoisndashWellington for the benthic component (Figure 7) Sample locations were arranged in three pairs within the river For each pair there was a bank site (depth approximately 4 m) and a channel site located approximately halfway across the river Sampling locations of the pairs were located at the JervoisndashWellington outflow and approximately 200 m upstream and 165 m downstream from the discharge point All samples were collected on 16 April 2013

A Wildco sediment grab was also used to collect samples of macro-invertebrates in the benthic zone (living on and within the riverbed sediment) At each sampling location three replicate grab samples were collected each consisting of 500 ml of sediment Samples were sieved through a 250-microm mesh and preserved with 90 ethanol in situ Macro-invertebrate identification was later undertaken within the laboratory to the lowest taxonomic level possible

Benthic data were entered into a Microsoft Excel spreadsheet and values for abundance and richness were populated Further analyses were undertaken using PRIMER v6 with the PERMANOVA+ add on (Anderson et al 2008) The Pieloursquos evenness index was calculated in PRIMER using the DIVERSE routine A resemblance matrix was calculated using the BrayndashCurtis similarity measure and from this the PERMANOVA (permutation based ANOVA) routine was used to test differences between both the location of samples (upstream discharge point and downstream) and bank and main channel habitats Finally SIMPER analyses were undertaken to determine the contributions of taxa to the dissimilarity of groups of samples (eg bank vs main channel habitat)

Figure 7 Benthic sediment sampling locations

13 Water quality parameters The water quality parameters considered in this report were salinity temperature pH alkalinity acidity major ions (sulfate chloride calcium magnesium potassium fluoride) and total and dissolved (lt04 microm) metals (primarily iron aluminium and manganese)

A brief description of some of the key water quality parameters as follows

bull pH is an indicator of acidity or alkalinity Neutral water has a pH of 65 acidic solutions have lower values and alkaline solutions have higher values

16

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
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Page 16: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

bull Alkalinity is a measure of the buffering capacity of water or the capacity of the water to neutralise acids and resist pH change Alkalinity within water bodies is consumed as acid as released from acid sulfate soils Adding neutralising agents (eg hydrated lime limestone) contributes alkalinity to waters helping to neutralise any acid released from the sediments

bull Acidity is a measure of the amount of hydrogen ions and dissolved aluminium manganese and iron in the water Acidity is not normally present in surface waters unless they are impacted by acid sulfate soil or mine impacts

bull Salinity is a measure of the amount of dissolved salts in the water Saline water conducts electricity more readily than freshwater so electrical conductivity (EC microScm) is routinely used to measure salinity As salinity increases it may become toxic to native freshwater organisms

bull Metals such as iron aluminium and manganese are measured primarily to determine interactions between sediments and receiving ground or surface water bodies If exposed acid sulfate sediments acidify and the soil pH is reduced metals that have been previously unavailable and bound up within sediment are released Any subsequent increase in metal concentration in the water body can be used as an indicator of acid sulfate soil impacts Metals can be toxic to aquatic ecosystems and human health at elevated levels

bull Sulfatechloride ratio is used to give an indication of any sulfate inputs to the water body from acid sulfate soils Chloride concentration is largely determined by evaporation and dilution An increase in the ratio of sulfate to chloride indicates possible external sulfate inputs such as from acid sulfate soils

14 Water sampling and analytical methods Samples in the salt drains were taken by grab sampling directly adjacent to the pump shed using a clean plastic bucket andor groundwater bailer

Plume sampling was conducted aboard a 55-m aluminium vessel Samples were collected at the surface by grab samples and samples at depth middle and bottom of water were collected using a Van Dorn sampling unit

New sample bottles washed and rinsed with de-ionised water were used for all analyses Samples were collected by rinsing the bottle with the sample and collecting the sample according to standard methods (APHA 2005 and previous editions) Following collection the water samples were transported to the laboratory in ice-filled cooler boxes and then stored at 4ordmC Temperature pH ORP EC and dissolved oxygen were measured at the time of sample collection using calibrated instruments (YSI Pro Plus multi-parameter meters)

All other analysis was undertaken by the Australian Water Quality Centre (AWQC) or ALS Melbourne both are National Association of Testing Authorities (NATA) accredited laboratories NATA accreditation requires maintenance and documentation of strict quality control procedures

Salinity was measured according to manufacturersrsquo instructions using calibrated conductivity meters Water alkalinity was measured by titration with H2SO4 to a pH 45 end-point and acidity was measured by titration with a base (eg NaOH) to an endpoint (pH asymp 83) (APHA 2005) Dissolved (lt04 microm) metal concentrations were measured by ICPndashMass Spectrometry

17

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 17: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

2 Results 21 Salt drain sampling results The graphs within this section illustrate the trend in pH and salinity since initial monitoring began in February 2011 and acidity alkalinity and metals concentrations based on laboratory analysis since July 2012 The graphs are separated for ease of interpretation and visualisation between those drains south of Murray Bridge (between Murray Bridge and Wellington) and those north of Murray Bridge (between Murray Bridge and Mannum) See Figure 4 for more detail

211 Acidity and pH

Figures 8 and 9 show the pH results of 12 acidic salt drains in the LMRIA pH within the salt drains predominantly ranges between 3ndash6 pH units The ANZECC guidelines for freshwater ecosystems suggest a lower limit of pH 65 for aquatic health (ANZECC 2000) As such the majority of salt drains have a pH below the appropriate guidelines

Some recovery has been observed at Toora since January 2013 this property is not regularly irrigated and this recovery may be a result of alkaline inputs from the regional groundwater table Recent spikes in alkalinity (Figure 12) and salinity (Figure 14) support this Mobilong south of Murray Bridge has consistently reported low pH Mobilong is a retired irrigation area and as such has not regularly been irrigated since the drought occurred Extensive oxidation of acid sulfate soils has been able to take place as groundwater levels have receded Unlike Toora it appears there is minimal regional groundwater inputs as little to no alkalinity was recorded (Figure 13)

Acidity in salt drains south of Murray Bridge was initially high at most sites but trended down since August 2012 (note gaps or discontinuation in data for example at Burdett is a result of a lack of water within drains) Since then acidity has stabilised below 200 mgL at all sites (Figure 10) Comparatively acidity north of Murray Bridge has been more variable with higher concentrations and spikes then south of Murray Bridge The spikes in pH and acidity north of Murray Bridge are likely a result of in frequent irrigation and rainfall events allowing time for drawdown of the groundwater table and the oxidation of acid sulfate soils For example spike in acidity reported at Mobilong coincide with irrigation events undertaken in late 2012 at the request of the EPA Sites south of Murray Bridge are typically irrigated on a more regular timescale reducing fluctuations in groundwater levels and thus limiting the exposure of acid sulfate soils

LMRIA Salt drain pH south of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point Westbrook Park

Figure 8 Salt drain pH for drains south of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

18

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
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Page 18: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt drain pH north of Murray Bridge

0

1

2

3

4

5

6

7

8

9

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-May-12 19-Aug-12 07-Dec-12 27-Mar-13 15-Jul-13

pH

Pompoota Toora Mobilong Long Flat Burdett

Figure 9 Salt drain pH for drains North of Murray Bridge the red line shows the lower ANZECC (2000) guideline (pH 65) for protection of aquatic ecosystems

LMRIA Salt Drain Acidity- South of Murray Bridge

0

200

400

600

800

1000

1200

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 10 Acidity concentrations for salt drains south of Murray Bridge

19

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

200

300

400

500

600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
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Page 19: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Acidity- North of Murray Bridge

0

100

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600

700

800

900

1000

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Acid

ity (m

gL

as C

aCo3

)

Long Flat Pompoota Burdett Toora Mobilong

Figure 11 Acidity concentrations for salt drains North of Murray Bridge

212 Alkalinity

Despite high acidity concentrations alkalinity persists in small concentrations in some of the acidic salt drains In the south of Murray Bridge a marked improvement in alkalinity concentrations was observed at several sites Kilsby had the most significant improvement with concentrations steadily increasing since September 2012 Kilsby is not regularly irrigated with the EPA unaware of irrigation events post-drought As such the greatest contributions of water to this salt drain are from rainfall events and regional groundwater seepage (regional groundwater in this area is classified as having high alkalinity) Minimal surface contributions from infrequent rainfall and irrigation would also reduce flushes of sulfuric material out of the soil profile into the salt drains Toora to the north of Murray Bridge (Figure 13) similarly is not regularly irrigated and is possibly heavily influenced by alkaline regional groundwater and an absence of flushing into the salt drain

20

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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                                    • ColumnTitle_2
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Page 20: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Alkalinity- South of Murray Bridge

0

100

200

300

400

500

600

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 12 Alkalinity concentrations within salt drains south of Murray Bridge

LMRIA Salt Drain Alkalinity- North of Murray Bridge

0

50

100

150

200

250

300

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Alka

linity

(mg

L as

CaC

o3)

Long Flat Pompoota Burdett Toora Mobilong

Figure 13 Alkalinity concentrations within salt drains north of Murray Bridge

213 Salinity

Figures 14 and 15 report the salinity results for acidic salt drains throughout the sampling period Results suggest a decreasing trend in salinity at all sites most likely due to increased rainfall and irrigation events diluting the highly saline waters experienced in the drought Mobilong continues to have the highest salinity north of Murray Bridge due to the lack of active irrigation and pumping events Higher salinities recorded at Mobilong Toora and Pompoota are likely due to their local hydrogeology (Barnett 2003)

21

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
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Page 21: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

11 12 12 12

LMRIA acid drainge monitoring report 2013

LMRIA Salt drain salinity south of Murray Bridge

0

2000

4000

6000

8000

10000

12000

14000

16000

18000

20000

16-Feb-11 06-Jun-11 24-Sep-11 12-Jan-12 01-Mayshy12

19-Augshy12

07-Dec-12 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Jervois (Wellington End) Riverglen Jervois (Woods Point end)

Monteith Woods Point

Figure 14 Salt drain salinity (electrical conductivity) south of Murray Bridge

LMRIA Salt drain salinity north of Murray Bridge

0

5000

10000

15000

20000

25000

30000

35000

16-Feb-11 06-Jun-11 24-Sepshy 12-Jan-12 01-Mayshy 19-Augshy 07-Decshy 27-Mar-13 15-Jul-13

Elec

trica

l Con

duct

ivity

(EC)

Pompoota Toora Mobilong Long Flat Burdett

Figure 15 Salt drain salinity (electrical conductivity) north of Murray Bridge

214 Metals

Figures 16ndash31 report total and soluble metal concentrations of the acidic salt drains throughout the monitoring program Salt drains south of Murray Bridge have reported predominantly decreasing concentrations of iron (Fe) manganese (Mn) and aluminium (Al) This is likely a result of an initial flushing of metals released during the acid sulfate soil (such as pyrite) oxidation process Metal concentrations at sites north of Murray Bridge have also generally decreased but with greater variability and concentration spikes Mobilong has been the most variable site with several large spikes in Fe Mn and Al

All acidic salt drains sampled reported at least one exceedence of water quality guidelines many with multiple metal exceedences Tables 1 and 2 detail metal concentrations and exceedences of the Australian Water Quality guidelines for

22

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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                                    • ColumnTitle_2
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Page 22: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

human health and aestheic use prepared by the National Health and Medical Research Council (NHMRC) as well as the ANZECC guidelines for aquatic ecosystems Despite decreases in total nickel (Ni) at all sites (Figures 24 and 25) reported concentrations were above NHMRC health guidelines and ANZECC guidelines It should be noted that once the drain water is discharged into the river it undergoes rapid dilution reducing these high concentrations (discussed in greater detail in 321 Discharge mixing results)

Soluble metals generally have a greater bio-availability and mobility then total metals within an environment (Clemente et al 2002) Soluble Al has predominantly decreased at all sites to below 10 mgL Soluble Fe and Mn have been highly variable with multiple concentration spikes and concentrations north of Murray Bridge have been predominantly highest Mobilong has consistently had the highest concentrations of soluble metals most likely a result of low pH (Figure 9) improving the solubility of metals in water

23

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
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Page 23: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Aluminium- South of Murray Bridge

0

10

20

30

40

50

60

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 16 Total aluminium concentrations for LMRIA salt drains south of Murray Figure 17 Total aluminium concentrations for LMRIA salt drains north of Murray Bridge Bridge

LMRIA Salt Drain Total Arsenic- South of Murray Bridge

0

0002

0004

0006

0008

001

0012

0014

0016

0018

002

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Ars

enic

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Arsenic- North of Murray Bridge

0

0005

001

0015

002

0025

003

0035

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

rsen

ic (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 18 Total Arsenic concentrations for LMRIA salt drains south of Murray Bridge Figure 19 Total Arsenic concentrations for LMRIA salt drains north of Murray Bridge

24

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 24: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Total Iron- South of Murray Bridge LMRIA Salt Drain Total Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Iro

n (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

320

270

220

170

120

70

20

10072012 -30 29082012 18102012 7122012 26012013 17032013 6052013

Tota

l Iro

n (m

gL)

Date

Riverglen Woods Point Jervois Woods Point Jervois Wellington Monteith

Westbrook Park Kilsby

Figure 20 Total iron concentrations for LMRIA salt drains south of Murray Bridge Figure 21 Total iron concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Total Manganese- South of Murray Bridge

0

5

10

15

20

25

30

35

40

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Total Manganese- North of Murray Bridge

0

5

10

15

20

25

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Man

gane

se (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

Figure 22 Total manganese concentrations for LMRIA salt drains south of Figure 23 Total manganese concentrations for LMRIA salt drains north of Murray Murray Bridge Bridge

25

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
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Page 25: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain Total Nickel- South of Murray Bridge

0

01

02

03

04

05

06

07

08

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Kilsby Monteith

LMRIA Salt Drain Total Nickel- North of Murray Bridge

0

02

04

06

08

1

12

14

16

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Nic

kel (

mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 25 Total nickel concentrations for LMRIA salt drains north of Murray Bridge Figure 24 Total nickel concentrations for LMRIA salt drains south of Murray Bridge

Figure 26 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Manganese- South of Murray Bridge

0

2

4

6

8

10

12

14

16

18

20

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Man

gane

se (m

gL)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 27 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Manganese- North of Murray Bridge

0

2

4

6

8

10

12

14

16

18

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date So

lubl

e M

anga

nese

(mg

L)Long Flat pompoota Burdett Toora Mobilong

26

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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Page 26: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

LMRIA Salt Drain Soluble Iron- South of Murray Bridge

0

10

20

30

40

50

60

70

80

90

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

LMRIA Salt Drain Soluble Iron- North of Murray Bridge

0

50

100

150

200

250

300

350

400

450

500

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Solu

ble

Iron

(mg

L)

Long Flat Pompoota Burdett Toora Mobilong

Figure 28 Soluble iron concentrations for LMRIA salt drains south of Murray Figure 29 Soluble iron concentrations for LMRIA salt drains north of Murray Bridge Bridge

Figure 30 Soluble manganese concentrations for LMRIA salt drains south of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- South of Murray Bridge

0

5

10

15

20

25

30

35

40

45

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

Tota

l Alu

min

ium

(mg

L)

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 31 Soluble manganese concentrations for LMRIA salt drains north of Murray Bridge

LMRIA Salt Drain Soluble Aluminium- North of Murray Bridge

0

10

20

30

40

50

60

70

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date To

tal A

lum

iniu

m (m

gL)

Long Flat Pompoota Burdett Toora Mobilong

27

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 27: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Table 1 LMRIA salt drain water quality south of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC guidelines for aquatic ecosystems (green) Note these exceedences are in the undiluted drain water discharging to the river Substantial dilution occurs in the immediate discharge zone and river Units are in mgL

Date Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Westbrook Park 11072012 17 lt0005 lt0003 0034 0011 043 0001 lt0001 0143 0003 501 0002 124 lt00003 lt0001 0259 0179

Westbrook Park 13082012 748 lt0005 lt0003 0078 0004 11 lt0001 lt0001 0147 0003 946 lt0001 924 lt00003 lt0001 0262 0125

Westbrook Park 03092012 131 lt0005 0004 0081 0012 145 lt0001 0003 0183 0007 629 0003 106 lt00003 lt0001 0308 0161

Westbrook Park 05102012 107 lt0005 lt0003 0059 0011 056 0001 0001 0188 0002 142 0002 962 lt00003 lt0001 0342 0191

Westbrook Park 05112012 309 lt0005 lt0003 0108 lt0003 lt0001 lt0001 0007 0003 715 lt0001 342 lt00003 lt0001 0019 0005

Westbrook Park 16012013 0073 lt0005 lt0003 0072 lt0003 146 lt0001 lt0001 0072 lt0001 672 lt0001 123 lt00003 lt0001 01 0024

Westbrook Park 11022013 0034 lt0005 lt0003 006 lt0003 198 lt0001 lt0001 0002 0001 147 lt0001 0348 lt00003 lt0001 0016 0003

Westbrook Park 01032013 0544 lt0005 lt0003 0095 lt0003 07 lt0001 lt0001 0097 0001 21 lt0001 129 lt00003 lt0001 0177 0051

Westbrook Park 11042013 0022 lt0005 lt0003 0056 lt0003 119 lt0001 lt0001 0008 0002 0121 lt0001 557 lt00003 lt0001 0037 0012

Woods Point 11072012 164 lt0005 0003 0042 lt0003 027 lt0001 lt0001 0104 lt0001 lt0001 359 lt00003 lt0001 0151 0101

Woods Point 13082012 27 lt0005 lt0003 0037 lt0003 029 lt0001 lt0001 0109 0002 252 0006 389 lt00003 lt0001 0171 0125

Woods Point 03092012 1816 lt00005 00016 00353 00024 033 00004 0001 01036 00028 1758 00005 329 lt000003 lt00001 01441 0084

Woods Point 05102012 0206 lt0005 lt0003 0058 lt0003 023 lt0001 lt0001 0022 0007 349 lt0001 133 lt00003 lt0001 0035 0042

Woods Point 05112012 0163 lt00005 0002 0035 lt00003 lt00001 lt00001 00131 00026 2028 00003 158 000009 00005 00207 00134

Woods Point 05122012 037 lt0005 lt0003 0049 lt0003 034 lt0001 lt0001 0046 0003 668 lt0001 188 lt00003 lt0001 007 0044

Woods Point 16012013 0363 00005 0002 00587 lt00003 0433 00002 00023 00322 00058 1159 00131 239 000005 00009 00449 01224

Woods Point 11022013 0178 lt00005 00022 00446 lt00003 0363 lt00001 00004 00163 00017 7759 00002 0993 lt00003 00018 00258 00063

Woods Point 01032013 0105 lt00005 00038 00389 lt00003 0325 lt00001 00006 00166 00016 9836 00007 11 lt000003 00012 00257 0008

Woods Point 22042013 0251 lt00005 00032 00495 lt00003 026 lt00001 00005 00258 00023 3971 00002 122 000008 00006 00349

Jervois-Wellington 11072012 664 lt0005 0003 0031 001 lt02 0001 0001 0226 0003 312 lt0001 764 lt00003 lt0001 0262 0191

Jervois-Wellington 13082012 1226 lt00005 0004 0028 00023 0185 00008 00007 01386 00028 193 00012 424 000005 00002 01389 00847

Jervois-Wellington 03092012 2148 lt00005 00078 00309 00024 0171 00005 00018 0161 00032 5206 00009 355 000003 00002 01473 00607

Jervois-Wellington 05102012 17 lt0005 lt0003 003 0004 lt02 lt0001 lt0001 0116 0007 103 0002 291 lt00003 lt0001 0126 0082

Jervois-Wellington 05112012 2713 lt00005 00008 00164 00038 0158 00004 00008 01042 00022 2315 00005 388 lt000003 lt00001 00954 00505

Jervois-Wellington 05122012 147 lt0005 lt0003 0028 0004 025 lt0001 lt0001 0182 0003 472 lt0001 577 lt00003 lt0001 0193 0108

Jervois-Wellington 16012013 0648 lt00005 00038 0034 00008 0186 00002 00018 01063 00036 1032 0002 378 lt00003 lt00001 01002 00638

Jervois-Wellington 11022013 267 lt00005 00026 00254 00009 0238 00002 00019 00592 00058 3274 00007 186 lt00003 lt00001 00681 00348

Jervois-Wellington 13032013 0222 lt00005 0002 00448 00005 0254 00003 00005 00673 00023 5452 00003 263 000011 lt00001 00521 0021

Jervois-Wellington 11042013 3733 lt00005 00022 00431 00039 0326 00004 00004 02835 00024 4434 00004 802 lt000003 lt00001 02439 01023

Jervois-Woods Pt 11072012 139 lt0005 lt0003 0026 0016 043 0001 lt0001 0218 0003 213 lt0001 767 lt00003 lt0001 031 0255

Jervois-Woods Pt 13082012 176 lt0005 lt0003 0027 0018 052 0001 lt0001 0397 0008 143 0031 999 lt00003 lt0001 0534 0379

Jervois-Woods Pt 03092012 1257 lt00005 0002 00198 00128 047 00014 00014 03711 08922 1812 00031 731 000005 lt00001 04429 02472

Jervois-Woods Pt 05102012 556 lt0005 lt0003 004 0009 021 lt0001 0001 0192 0071 371 0002 363 lt00003 lt0001 0268 021

Jervois-Woods Pt 05112012 1225 lt00005 00025 00328 00007 00001 00003 00439 00045 9483 00004 181 lt000003 00001 00546 00356

Jervois-Woods Pt 05122012 559 lt0005 lt0003 0042 001 037 lt0001 lt0001 0238 0008 533 0001 541 lt00003 lt0001 03 0174

Jervois-Woods Pt 16012013 3617 lt00005 00018 00406 00038 0309 00005 0001 01355 0006 7318 00029 362 lt00003 lt00001 01707 01188

Jervois-Woods Pt 11022013 2644 lt00005 00019 00394 00046 0392 00004 00004 01156 00028 3332 00005 293 lt000003 lt00001 01571 008

Jervois-Woods Pt 13032013 2011 lt00005 00017 00463 0003 0426 00003 00008 01071 00031 18 00009 292 000004 lt00001 01466 00716

Jervois-Woods Pt 22042013 28 lt00005 0003 00482 00037 0412 00005 00012 01213 00045 2727 00007 368 000004 00002 01643 00867

Kilsby 26072012 446 lt0005 lt0003 0056 0028 068 0003 0003 0395 0006 597 lt0001 154 lt00003 lt0001 0708 0362

Kilsby 13082012 488 lt0005 0007 0043 0025 058 0004 0001 0306 0006 129 0003 153 lt00003 lt0001 0602 0412

Kilsby 03092012 1252 lt00005 00072 00627 00082 0503 00015 00008 0148 00022 1651 00004 546 000004 00001 0244 01128

Kilsby 05102012 0817 lt0005 001 0081 lt0003 056 lt0001 lt0001 0093 lt0001 478 lt0001 492 lt00003 lt0001 014 0082

Kilsby 05112012 1891 lt00005 00109 00527 lt00003 00001 00007 00146 00034 5898 00008 196 lt000003 00004 00182 00158

Kilsby 05122012 0297 lt0005 0018 0066 lt0003 048 lt0001 lt0001 0008 0001 388 lt0001 132 lt00003 lt0001 0011 0021

Kilsby 16012013 0136 lt00005 00045 00483 lt00003 0463 lt00001 00007 00036 00005 1376 00008 0906 000005 00006 00072 00153

Kilsby 11022013 0195 lt00005 00172 0076 lt00003 0482 lt00001 00005 00044 00002 35 00001 0939 lt00003 00008 00064 00055

Kilsby 13032013 0067 lt00005 00033 0066 lt00003 0525 lt00001 00004 00035 00006 4348 lt00001 0808 lt000003 00007 00058 00054

Kilsby 11042013 0035 lt00005 00036 00693 lt00003 0556 lt00001 00004 0004 00005 6026 lt00001 000004 00005 00057 00056

Montieth 11072012 0656 lt0005 0011 0055 lt0003 041 lt0001 0001 0257 0001 108 lt0001 521 lt00003 lt0001 0252 0134

Montieth 13082012 328 lt0005 0014 0043 0008 043 lt0001 lt0001 0511 0004 185 0001 105 lt00003 lt0001 0543 0353

Montieth 03092012 1826 lt00005 00024 00476 00034 0211 00004 00013 0218 00023 4554 00003 363 lt000003 lt00001 0212 01162

Montieth 05102012 278 lt0005 lt0003 0049 0006 lt02 lt0001 0001 0235 0006 19 0002 438 lt00003 lt0001 0248 018

Montieth 05112012 115 00005 00046 00349 00024 033 00001 00017 02177 00029 4751 00005 412 lt000003 lt00001 02029 01098

Montieth 05122012 124 lt0005 0003 0035 lt0003 034 lt0001 lt0001 0072 0003 281 lt0001 146 lt00003 lt0001 0084 0054

Montieth 16012013 0603 00005 0007 00398 00006 0343 00002 00036 0085 0006 3601 00119 163 lt00003 00004 0086 01373

Montieth 11022013 0162 00005 00012 00384 lt00003 0269 lt00001 00004 0049 00011 234 00002 157 lt00003 lt00001 00498 00162

Montieth 01032013 0186 lt00005 00046 00456 lt00003 0308 lt00001 00009 00352 00016 3273 00006 183 000004 00002 00376 00131

Montieth 11042013 0063 lt00005 00028 00451 lt00003 0782 lt00001 00008 00408 0002 7255 00001 107 000003 00005 00418 00137

Riverglen 11072012 0817 lt0005 0007 0071 lt0003 109 lt0001 0001 0149 0003 329 lt0001 254 lt00003 0004 0178 0097

Riverglen 13082012 0091 lt0005 0004 0077 lt0003 099 lt0001 lt0001 0093 0005 635 0004 212 lt00003 0006 0116 0051

Riverglen 03092012 0088 lt0005 0004 0077 lt0003 124 lt0001 0001 0096 0003 438 lt0001 171 lt00003 0005 012 0042

Riverglen 05102012 13 lt0005 0013 0042 lt0003 028 lt0001 0001 0217 0005 911 lt0001 425 lt00003 lt0001 0201 0163

Riverglen 05112012 3443 lt00005 00166 0034 00021 00005 00012 01827 00046 1262 00012 371 lt000003 00002 02116 01746

Riverglen 05122012 0069 lt0005 0004 0055 lt0003 049 lt0001 lt0001 0028 0004 565 lt0001 146 lt00003 0002 004 002

Riverglen 16012013 0085 lt00005 00037 00446 lt00003 0305 lt00001 0001 00704 00016 1092 00012 147 lt00003 00002 00758 00329

Riverglen 11022013 0038 00011 00068 00336 lt00003 027 lt00001 00006 00077 00009 1184 lt00001 0503 lt000003 00026 00154 00033

Riverglen 01032013 0048 lt00005 00047 00409 lt00003 0301 lt00001 00004 00075 00043 3681 00001 0415 000013 00031 00182 00029

Riverglen 11042013 0038 lt00005 00027 00416 lt00003 0218 lt00001 00004 0003 00027 3692 lt00001 0199 lt000003 00017 00122 00061

28

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 28: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Table 2 LMRIA salt drain water quality north of Murray Bridge exceedences of drinking water (NHMRCNRMMC 2011) health (red) and aesthetic (yellow) guidelines as well as the ANZECC Guidelines for aquatic ecosystems (green)

Date

Aluminium shyTotal

Antimony shyTotal

Arsenic shyTotal

Barium shyTotal

Beryllium shyTotal

Boron shySoluble

Cadmium shyTotal

Chromium shyTotal

Cobalt shyTotal

Copper shyTotal

Iron shyTotal

Lead shyTotal

Manganese shyTotal

Mercury shyTotal

Molybdenum shyTotal

Nickel shyTotal Zinc - Total

Health 0003 001 07 4 0002 005 2 001 05 0001 005 002

Aethetic 02 1 03 01 3

ANZECC 00008 0009 0013 037 00002 00033 00014 00014 03 00034 19 00006 0023 0011 0006

Burdett 11072012 0443 lt0005 lt0003 0037 lt0003 022 lt0001 lt0001 0116 0002 162 lt0001 261 lt00003 lt0001 0107 0081 Burdett 13082012 0422 0001 00026 00384 00004 0282 00001 00004 00444 00029 7011 00005 1259 000005 0001 00607 00224 Burdett 03092012 3357 lt00005 00022 00267 00034 0178 00008 00011 02401 00043 7306 00005 354 000005 lt00001 024 01161 Burdett 05102012 20 lt0005 0007 0068 0018 lt02 0004 0003 0542 0024 497 0007 85 lt00003 lt0001 0612 0593 Burdett 05112012 197 lt0005 0006 003 0013 029 lt0001 0004 0463 0008 135 0003 898 lt00003 lt0001 0542 0357 Burdett 05122012 509 lt0005 0009 0031 0007 024 lt0001 0001 0393 0004 221 lt0001 685 lt00003 lt0001 0441 0226 Long Flat 11072012 0249 lt0005 0012 0069 lt0003 04 lt0001 0003 0138 0001 295 lt0001 419 lt00003 lt0001 0141 0095 Long Flat 13082012 0269 0001 00261 00416 00011 0225 00002 00009 00908 00033 4707 00008 2784 000007 00001 00774 00692 Long Flat 03092012 0402 lt00005 00169 00398 00013 0222 00002 00011 01082 00034 3841 00006 251 lt000003 lt00001 00927 00685 Long Flat 05102012 0177 lt0005 0015 0052 lt0003 032 lt0001 lt0001 01 lt0001 255 lt0001 317 lt00003 lt0001 0096 0075 Long Flat 05112012 0566 lt00005 00105 00547 00008 0558 lt00001 00013 01053 00034 1641 00005 313 lt000003 00005 01048 00542 Long Flat 05122012 0149 lt0005 0025 0046 lt0003 022 lt0001 0002 0071 0004 407 lt0001 242 lt00003 lt0001 007 0053 Long Flat 31012013 0326 lt00005 00292 00466 lt00003 0169 lt00001 00013 00322 00046 3493 00013 121 00004 00003 00325 00197 Long Flat 11022013 0224 lt00005 00162 00466 00007 0326 00002 00011 01074 00032 3144 00005 216 lt00003 00002 01084 0062 Long Flat 01032013 0153 lt00005 00168 0047 lt00003 0315 lt00001 0001 00577 00023 4852 00008 244 000005 00004 00496 00208 Long Flat 11042013 0155 lt0005 0027 0057 lt0003 045 lt0001 lt0001 0065 0003 298 lt0001 268 lt000003 00001 007 0045 Mobilong 11072012 075 001 lt0003 0079 lt0003 148 0001 0001 0221 0001 521 lt0001 548 lt00003 lt0001 0222 0164 Mobilong 13082012 803 lt0005 0003 008 0013 157 0003 lt0001 0555 0005 813 0004 889 lt00003 lt0001 0598 0451 Mobilong 03092012 637 lt0005 0016 0039 0036 079 0009 0006 131 002 259 0005 156 lt00003 lt0001 141 089 Mobilong 05102012 264 lt0005 0005 0039 0025 086 0005 0002 0793 0013 275 0006 104 lt00003 lt0001 0841 0582 Mobilong 05112012 537 lt0005 0007 0016 0016 lt02 0004 0001 0736 0012 148 0004 133 lt00003 lt0001 0796 0615 Mobilong 05122012 285 lt0005 0014 0015 0021 095 0002 0004 101 0005 366 0001 234 lt00003 lt0001 0981 0409 Mobilong 16012013 491 lt0005 0018 004 0004 067 lt0001 0003 0568 0001 474 0002 142 lt00003 lt0001 046 019 Mobilong 01032013 1577 lt00005 00036 00159 00107 0504 00015 00009 02034 00126 1334 0003 23 lt00003 lt00001 02671 01045 Mobilong 11042013 37 lt0005 0004 0042 0004 062 lt0001 lt0001 0287 0002 845 lt0001 705 lt00003 lt0001 0248 0128 Pompoota 11072012 288 lt0005 0015 0022 0008 046 0002 0001 028 0006 65 lt0001 588 lt00003 lt0001 035 0241 Pompoota 13082012 46 lt0005 0014 0025 0008 053 0002 lt0001 0392 0007 855 0003 87 lt00003 lt0001 0476 03 Pompoota 03092012 2698 lt00005 00064 00274 00028 0424 00012 00022 0232 00064 5931 00013 518 000004 00003 0231 01515 Pompoota 05102012 232 lt0005 0005 0035 0005 061 0001 0001 0283 0003 536 0001 675 lt00003 lt0001 0316 0223 Pompoota 05112012 227 lt0005 0008 0031 lt0003 lt02 0001 lt0001 0325 001 909 0002 113 lt00003 lt0001 033 0227 Pompoota 05122012 074 lt0005 0007 0028 lt0003 102 lt0001 0001 0482 0003 277 lt0001 147 lt00003 lt0001 0422 0225 Pompoota 16012013 0925 lt00005 00015 00316 00027 053 00007 00011 01911 00027 2223 0001 51 lt00003 lt00001 01997 01205 Pompoota 11022013 0304 lt0005 lt0003 0044 lt0003 092 lt0001 lt0001 0181 0002 388 lt0001 859 000008 lt0001 0201 0065 Pompoota 01032013 0376 00006 00017 00328 00015 0484 00006 00004 01515 00017 6162 00006 481 lt000003 lt00001 01616 00686 Pompoota 11042013 106 lt0005 0004 0043 lt0003 074 lt0001 lt0001 0177 0004 164 lt0001 57 lt000003 00006 02 017 Toora 11072012 221 lt0005 0014 004 0005 082 0002 0001 0409 0002 907 lt0001 538 lt00003 lt0001 0428 0304 Toora 13082012 585 lt0005 0022 0041 0011 068 0002 lt0001 0742 0005 149 0004 804 lt00003 lt0001 0753 0473 Toora 03092012 173 lt0005 0012 0045 0004 072 0001 0002 072 0003 146 lt0001 711 lt00003 lt0001 0679 0374 Toora 05102012 0751 lt0005 lt0003 0063 lt0003 084 lt0001 lt0001 0336 lt0001 407 lt0001 469 lt00003 lt0001 0315 0159 Toora 05112012 372 lt0005 lt0003 0057 0003 lt02 lt0001 lt0001 032 0007 27 0001 573 lt00003 lt0001 0322 0199 Toora 05122012 0684 lt0005 lt0003 0083 lt0003 033 lt0001 lt0001 015 0002 699 lt0001 196 lt00003 lt0001 0151 0084 Toora 16012013 1529 lt00005 00026 0099 00023 0404 00004 00011 02502 00022 1339 00009 317 lt00003 lt00001 0226 01129 Toora 11022013 0281 00007 00081 00501 lt00003 0243 lt00001 00006 0031 00041 8804 00004 061 lt000003 00032 00361 00087 Toora 01032013 0197 lt00005 00037 0039 lt00003 0287 lt00001 00005 00511 00026 4719 00004 108 lt000003 00024 00536 00104 Toora 11042013 0366 lt00005 00022 00516 00007 0555 00002 00005 01778 00016 4382 00002 295 000003 00004 01687 00484

215 Sulfatechloride ratios

Figures 32 and 33 illustrates the highly variable sulfatechloride ratios for the acidic salt drains A general increasing trend of the ratio observed north of Murray Bridge may be indicative of increasing sulfate inputs from acid sulfate soils Southern drains are highly variable with JervoisndashWellington and JervoisndashWoods Point increasing since December 2012 The remaining sites are predominantly stable with some fluctuations that may be attributed to irrigation and rain events There are no consistent decreasing trends that might indicate sulfate reduction (natural remediation process) is occurring

29

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

30

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
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Page 29: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

LMRIA Salt Drain SO4Chloride Ratio- South of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Riverglen Woods Point Jervois Woods Point Jervois Wellington Westbrook Park Kilsby Monteith

Figure 32 Sulfatechloride ratio for salt drains south of Murray Bridge

LMRIA Salt Drain SO4Chloride Ratio- North of Murray Bridge

000

020

040

060

080

100

120

140

10072012 29082012 18102012 7122012 26012013 17032013 6052013

Date

SO4

Chlo

ride

Ratio

Long Flat Pompoota Burdett Toora Mobilong

Figure 33 Sulfatechloride ratio for salt drains north of Murray Bridge

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LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

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LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
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Page 30: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

22 Plume monitoring results

321 Plume mixing dynamics

The acid drainage discharges enter the River Murray from large pumps Typically pipes from these pumps discharge 1ndash2 m below the river level The discharge zone is typically a channel (5ndash10 m wide up to 30ndash40 m long Figure 34) that is connected to the main river channel

Figure 34 Discharge of acid drainage water into the River Murray

The LMRIA drain water is typically much more saline than the River Murray water (see Figure 14 for drain conductivities compared with 300ndash500 microScm conductivity for the river) The consequence of this is the drainage water is much denser than the receiving water body This causes the salt drain discharge to sink to the bottom of the river by the time it reaches the main channel The water quality parameters of pH and salinity can be used as indicators to track the plume in the River Murray channel

Results from a Jervois (Woods Point end) plume monitoring in October 2011 are shown in Figure 35 The plume water sinks to the bottom of the channel at the point of discharge and then is transported downstream at depth At Jervois (Woods Point end) the plume was detected up to 16 km downstream until it was dispersed (Figure 35) Similar trends were found at selected other sites Jervois (Wellington end) Figure 36 Long Flat Figure 37 and Westbrook Park Figure 38 It is noted that although the river pH in the vicinity of the drain discharges decreases (Figures 13ndash16) it is always within ANZECC guidelines for protection aquatic ecosystems (pH 65ndash90)

31

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 31: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Figure 35 pH and salinity in acid drainage plume discharged from Jervois (Woods Point end) irrigation area in October 2011

32

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
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Page 32: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Figure 36 pH and salinity in acid drainage plume discharged from Jervois (Wellington end) irrigation area in February 2013

33

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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                                    • ColumnTitle_3
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Page 33: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Figure 37 pH and salinity in acid drainage plume discharged from Long Flat irrigation area in November 2013

34

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
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Page 34: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Figure 38 pH and salinity in acid drainage plume discharged from Westbrook irrigation area in November 2013

35

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
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Page 35: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

The spatial extent of the plumes changed as the flows decreased Figure 39 shows the extent of the acid drainage plume from Long Flat irrigation area under high (13 November 2012) and low flows (5 March 2013) As the river flow decreased the plume zone expanded in extent both upstream and downstream This is due to slower dilution and mixing under the lower flow conditions Figure 40 shows metal results from the high and low flow sampling period shown in Figure 39 The results show that as expected slightly lower alkalinity values and elevated metal concentrations are seen in the bottom of the water column in the vicinity of the discharge

Figure 39 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

36

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
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                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 36: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

37

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
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Page 37: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Figure 40 Conductivity alkalinity and metals (total Fe soluble and total Mn total Ni) in the Long Flat acid drainage plume under high and low flows

38

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
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Page 38: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

The difference of plume behaviour between high and low flows is once again seen at Monteith irrigation area (Figure 41) Figure 42 shows how the higher salinityconductivity in the plume had a much greater effect throughout the water column under low flows compared to high flows

A general conclusion from the high and low flow plume comparison is that water quality risks expand somewhat under lower flows

Figure 41 Extent of the acid drainage plume from Monteith irrigation area under high and low flows

39

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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Page 39: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Dep

th (m

) D

epth

(m)

Conductivity Montieth 1 0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3 2 Montieth 4 4 Montieth 5 6 Montieth 6 8 Montieth 7

10 Montieth 8 12 Montieth 9 14 Monteith10 16

18 10012013 LMRIA Depth Profile- Monteith

Low flow 5 540 MLday

Conductivity Montieth 1

0 200 400 600 800 1000 1200 1400 Montieth 2

0 Montieth 3

2 Montieth 4

4 Montieth 5 6 Montieth 6 8 Montieth 7 10 Montieth 8 12 Montieth 9 14

16 18

26092012 LMRIA Depth Profile- Montieth High flow 41 300 MLday

Figure 42 Extent of the acid drainage plume from Long Flat irrigation area under high and low flows

221 Summary of data in comparison to water quality guidelines

To better assess the potential ecosystem and drinking water impacts arising from the acid drainage discharges the summary statistics for the LMRIA plume data were separately calculated for three regions

bull Table 3 Upstream ndash samples taken upstream from a particular acid drainage discharge

bull Table 4 Discharge ndash samples taken near the acid drainage discharges (where pump discharge channel meets main river channel asymp25 m mixing zone)

bull Table 5 Downstream ndash samples taken downstream of where a particular acid drainage discharge occurs

The upstreambaseline water quality data shows some exceedence of aquatic ecosystem (ANZECC 2000 protection of 95 of species) and drinking water quality guidelines (ADWG 2010) in Table 3 These exceedences mostly relate to the rsquonaturallylsquo high turbidity in the river The Fe and Al exceedences in particular relate to the clay content of the river turbidity Exceedences also occur for total Cd Cu and V but these concentrations are near the instrumental detection limit and unlikely to be bio-available given the neutral pH and high turbidity present (binds soluble metals) Nitrate also shows some exceedence of guidelines but this is consistent with previous research on nutrients in this reach of the river (Mosley and Fleming 2010)

40

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 40: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

In the discharge zone (Table 4) the exceedences noted above at the baseline site are still present as expected but there were no additional exceedences of median values This indicates on average the acid drainage discharges did not significantly impact the water quality of the main channel However some additional patterns emerge compared to the upstream data

As expected lower minimum and 25th percential pH values were found in the discharge zone but no data was below the ANZECC guidelines of pH 65 Additional metal exceedences also exist in the localised mixing zone that were not found in the upstream sites In particular exceedences for soluble metals (Al Fe Mn) and total (Al Cu Fe Mn V Zn) increase in the 75th percentile and maximum value statistics A few of the parameters (Na SO4 soluble Fe Cl) only exceeded guidelines for their maximum values In general the exceedences associated with the acid discharges and not present at the baseline sites (Table 3) are relatively minor This suggests the high concentrations of soluble metals in the drainage water (Tables 1 and 2) are being rapidly removed in the localised mixing zone

In the downstream mixing zone results (Table 5) water quality is comparable to the baseline sites (Table 6) A slight increase in median values and other summary statistics is found for total Fe and sulfate This relates to the acid sulfate-related water input but is a relatively minor impact

In general the water quality exceedences relating to the acid drainage discharges are minor andor confined to a localised mixing zone before the plume reaches the main river channel

41

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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                                    • ColumnTitle_3
                                    • ColumnTitle_3
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Page 41: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Table 3 Baseline summary statistics ndash upstream of where discharge occurs from a particular acid drain (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 47 40 68 20 144 na na na

Alkalinity mgL as CaCO3 82 54 101 49 123 na na na

Aluminium ndash Acid Soluble mgL 0091 0050 0118 0019 0252 na 02 0055

Aluminium ndash Soluble mgL 0031 0019 0078 0013 0234 na na 0055

Aluminium ndash Total mgL 28 14 61 07 146 na na 0055

Ammonia as N mgL 0017 0011 0026 0005 0102 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0002 0001 0002 0001 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0058 0047 0068 0040 0086 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0000 006 na na

Boron ndash Soluble mgL 0047 0035 0061 0020 0163 4 na 0370

Cadmium ndash Total mgL 0000 0000 0001 0000 0001 0002 na 00002

Calcium mgL 158 108 20 876 355 na na na

Chloride mgL 45 33 65 27 76 na 250 na

Chromium ndash Total mgL 0003 0001 0003 0001 0007 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0003 na na 00014

Conductivity microScm 325 246 426 193 12200 na 830 830

42

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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                                    • ColumnTitle_3
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Page 42: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0006 2 1 00014

DOC mgL 69 64 72 51 76 na na na

TDS (calc) mgL 172 128 217 98 261 na na na

Fluoride mgL 014 012 015 010 021 15 na na

Iron ndash Soluble mgL 0040 0016 0103 0006 0281 na 03 na

Iron ndash Total mgL 245 142 388 075 642 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0004 001 na 00034

Magnesium mgL 873 633 108 499 169 na na na

Manganese ndash Soluble mgL 0002 0001 0005 0000 0024 05 01 19

Manganese ndash Total mgL 0056 0045 0067 0022 0205 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0002 005 na na

Nickel ndash Total mgL 0003 0003 0004 0002 0006 002 na 0011

Nitrate + Nitrite mgL as N 0130 0079 0142 0008 0217 50 na 01

pH mgL 77 74 78 68 83 65 65 65

FRP mgL as P 0037 0028 0045 0003 0087 na na 004

Potassium mgL 558 368 66 321 128 na na na

Selenium ndash Total mgL 00001 00001 00001 00001 00005 001 na 0011

Silica ndash Reactive mgL 3 1 4 1 9 na 80 na

Sodium mgL 374 243 498 187 571 na 180 na

43

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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Page 43: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Sulfate mgL 137 84 164 63 225 na 250 na

Total Hardness mgL as CaCO3 67 53 94 43 109 na 200 na

Turbidity mgL 47 37 64 93 82 na na 50

Vanadium ndash Total mgL 0008 0006 0010 0003 0018 na na 0006

Zinc ndash Total mgL 0005 0003 0007 0001 0021 na 3 0008

44

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
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Page 44: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Table 4 Localised plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (Red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 59 51 104 25 200 na na na

Alkalinity mgL as CaCO3 770 540 980 420 1230 na na na

Aluminium ndash Acid Soluble mgL 0096 0057 0120 0019 3730 na 02 0055

Aluminium ndash Soluble mgL 0030 0018 0056 0008 0182 na na 0055

Aluminium ndash Total mgL 2307 1308 5202 0126 10460 na na 0055

Ammonia as N mgL 0021 0012 0075 0006 0939 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0002 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0003 001 na 0013

Barium ndash Total mgL 0063 0046 0066 0027 0077 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0005 006 na na

Boron ndash Soluble mgL 0050 0036 0075 0024 0124 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0000 0002 na 00002

Calcium mgL 189 129 230 87 4350 na na na

Chloride mgL 570 410 700 270 9920 na 250 na

Chromium ndash Total mgL 0002 0002 0004 0001 0005 005 na 00033

Cobalt ndash Total mgL 0001 0001 0002 0000 0150 na na 00014

Conductivity microScm 415 270 489 195 7180 na 830 830

45

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
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                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 45: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0002 0005 2 1 00014

DOC mgL 7050 6450 7300 5200 10300 na na na

TDS (calc) mgL 210 135 256 99 1110 na na na

Fluoride mgL 0140 0120 0170 0100 0770 15 na na

Iron ndash Soluble mgL 0029 0013 0096 0005 0704 na 03 na

Iron ndash Total mgL 2341 1270 3967 0316 9622 na 03 na

Lead ndash Total mgL 0001 0001 0002 0000 0007 001 na 00034

Magnesium mgL 108 80 123 51 2890 na na na

Manganese ndash Soluble mgL 0005 0002 0096 0000 3880 05 01 19

Manganese ndash Total mgL 0056 0045 0081 0009 3880 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0001 005 na na

Nickel ndash Total mgL 0004 0003 0006 0002 0245 002 na 0011

Nitrate + Nitrite mgL as N 0129 0055 0142 0003 0374 50 na 01

pH mgL 7700 7300 7800 6600 8000 65 65 65

FRP mgL as P 0030 0012 0040 0004 0088 na na 004

Potassium mgL 6020 4210 7210 3340 25900 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0000 001 na 0011

Silica ndash Reactive mgL 3000 2000 5000 1000 13000 na 80 na

Sodium mgL 461 284 579 183 8040 na 180 na

Sulfate mgL 168 117 192 69 4140 na 250 na

46

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
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Page 46: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 885 580 1073 420 3590 na 200 na

Turbidity mgL 510 400 620 100 1000 na na 50

Vanadium ndash Total mgL 0006 0005 0009 0001 0014 na na 0006

Zinc ndash Total mgL 0006 0004 0010 0002 0054 na 3 0008

47

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 47: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Table 5 Downstream plume summary statistics ndash inside immediate mixing zone (lt25 m from acid discharge data) of LMRIA (red = exceedence of ANZECC 2000 for aquatic ecosystems yellow = exceedence of ADWG 2010 for aesthetics blue = exceedence of ADWG 2010 for health)

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Acidity mgL as CaCO3 54 41 73 04 251 na na na

Alkalinity mgL as CaCO3 910 540 1020 240 1240 na na na

Aluminium ndash Acid Soluble mgL 0092 0055 0122 0019 0474 na 02 0055

Aluminium ndash Soluble mgL 0027 0018 0070 0004 0193 na na 0055

Aluminium ndash Total mgL 2630 1323 5907 0622 10400 na na 0055

Ammonia as N mgL 0017 0010 0038 0005 0347 na 05 09

Antimony ndash Total mgL 0001 0001 0001 0001 0001 0003 na na

Arsenic ndash Soluble mgL 0001 0001 0002 0000 0003 001 na 0013

Arsenic ndash Total mgL 0002 0002 0002 0001 0004 001 na 0013

Barium ndash Total mgL 0061 0049 0068 0038 0101 2 na na

Beryllium ndash Total mgL 0000 0000 0000 0000 0001 006 na na

Boron ndash Soluble mgL 0050 0037 0068 0020 0658 4 na 0370

Cadmium ndash Total mgL 0000 0000 0000 0000 0001 0002 na 00002

Calcium mgL 181 125 216 87 375 na na na

Chloride mgL 520 350 700 270 3330 na 250 na

Chromium ndash Total mgL 0002 0001 0003 0000 0010 005 na 00033

Cobalt ndash Total mgL 0001 0001 0001 0000 0047 na na 00014

Conductivity microScm 386 259 469 193 1470 na 830 830

48

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 48: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Copper ndash Total mgL 0003 0003 0004 0001 0111 2 1 00014

DOC mgL 6900 6500 7200 4600 8700 na na na

TDS (calc) mgL 205 129 251 98 792 na na na

Fluoride mgL 0140 0120 0160 0100 0260 15 na na

Iron ndash Soluble mgL 0040 0017 0107 0005 1260 na 03 na

Iron ndash Total mgL 2777 1264 3926 0693 11870 na 03 na

Lead ndash Total mgL 0002 0001 0002 0000 0008 001 na 00034

Magnesium mgL 102 69 120 50 428 na na na

Manganese ndash Soluble mgL 0003 0002 0008 0000 0585 05 01 19

Manganese ndash Total mgL 0055 0040 0075 0018 0632 05 01 19

Molybdenum ndash Total mgL 0001 0000 0001 0000 0007 005 na na

Nickel ndash Total mgL 0004 0003 0005 0001 0051 002 na 0011

Nitrate + Nitrite mgL as N 0126 0055 0141 0003 0204 50 na 01

pH mgL 7700 7500 7800 6600 8300 65 65 65

FRP mgL as P 0032 0022 0043 0005 0087 na na 004

Potassium mgL 5890 4120 6810 3240 8350 na na na

Selenium ndash Total mgL 0000 0000 0000 0000 0001 001 na 0011

Silica ndash Reactive mgL 3000 1000 4000 1000 9000 na 80 na

Sodium mgL 433 281 532 185 1700 na 180 na

Sulfate mgL 159 104 210 63 1880 na 250 na

49

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 49: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Parameter Unit Median 25th 75th Min Max Health Aesthetic ANZECC

Total Hardness mgL as CaCO3 890 538 1043 430 2700 na 200 na

Turbidity mgL 490 370 600 06 1800 na na 50

Vanadium ndash Total mgL 0007 0006 0010 0000 0025 na na 0006

Zinc ndash Total mgL 0005 0003 0008 0001 0032 na 3 0008

50

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 50: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

23 Sediment precipitate results Tables 6 and 7 illustrate the results of sediment samples collected within the river and precipitate sampling collected at the point of discharge Several sediment samples within the river were twice as high as the human health guidelines for manganese (500 mgkg) Sediment and precipitates falling out of suspension collected by sediment traps at the discharge point (Buoys Sediment trap) exceed health guidelines for manganese and environmental guidelines for arsenic and nickel Large volumes of aluminium and iron were found in both sediment samples and sediment traps ndash no ANZECC guideline value exist for these metals in sediment

Sediment collected from the salt drain had the highest concentrations of iron and aluminium including a concentration of 204 gkg of iron or 20 of the total sediments mass The upstream channel sample reported higher Al Mn and Fe concentrations than some of the downstream samples including directly at the discharge point This is unexpected but may be due to a different sediment composition in the zone around the discharge (eg less clay content)

The precipitation of solid metal oxyhydroxide phases occurs when the high concentrations of soluble metals in the acidic drainage water is neutralised upon mixing with river water (Simpson et al 2013) These precipitates appeared to settle rapidly in the immediate mixing zone as there was little change in total metal levels at the edge of the main channel or in the water downstream of the discharge

Table 6 Total recoverable metals in sediment and precipitates within the JervoisndashWellington drain and plume area ANZECC environmental investigation level guidelines (EIL) and health investigation level guidelines (HIL) utilised

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 10704 15449 15 104 03 175 169 196 10030 183 165 461 426 Discharge Point 8313 10800 11 51 01 183 144 155 3630 174 143 364 323 Downstream 4453 14054 14 99 00 237 63 208 4079 215 197 241 396 Downstream Channel 1 11966 18674 19 98 03 203 181 191 11302 203 170 479 472 Downstream Channel 2 11996 18350 18 91 06 190 185 197 12101 184 175 474 460 Buoys Sediment Trap 10938 55310 55 196 07 294 153 216 10470 272 212 741 772 Salt Drain Sediment 12927 204609 20 226 01 912 134 199 3581 1349 291 890 1530 ANZECC EIL 200 600 5000 600 3000 2000 ANZECC HIL 1000 5000 3000 2000

Table 7 Acid recoverable metals within JervoisndashWellington drain and plume area

Site ID Al microgg Fe microgg Fe As microgg Cd microgg Co microgg Cr microgg Cu microgg Mn microgg Ni microgg Pb microgg V microgg Zn microgg Upstream Channel 1638 6303 063 57 ltLOD 10 1 16 985 8 16 33 23 Discharge Point 1197 3574 036 22 ltLOD 14 1 10 309 9 13 22 13 Downstream 1591 10299 10 58 ltLOD 16 1 11 434 16 14 17 31 Downstream Channel 1 1792 7610 076 57 ltLOD 14 1 17 1107 9 19 36 25 Downstream Channel 2 1574 6861 069 52 ltLOD 13 1 15 1112 8 15 32 23 Buoys Sediment Trap 2689 46058 46 115 ltLOD 36 1 11 995 19 31 63 60 Salt Drain Sediment 8710 186054 186 174 ltLOD 101 5 13 411 134 30 72 169

24 Benthic ecology

241 Benthic abundance

A total of 967 individuals identified from the benthic samples collected at JervoisndashWellington (Table 8) Abundances at the three locations (upstream discharge point and downstream) did not differ significantly (pseudo-F215 = 057 P(perm) = 0668) The bank habitats had significantly higher abundances (mean 194plusmn13 individuals) compared with the channel habitats [mean 21plusmn2 individuals pseudo-F116 = 1972 P(perm) = 0001]

The SIMPER routine demonstrated that the taxa consistently contributing to the differences observed between the bank

and channel locations were higher abundances of Oligochaeta Nematoda and the presence of Cladopelma sp within the bank habitat (combined dissimilarity of 898) The abundances also differed significantly among sites [pseudo-F512 = 567 P(perm) = 0001] with highest abundances observed at the discharge point (SDP-1) and upstream (USB-1) bank

sites (Figure 43)

51

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 51: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

0

50

100

150

200

250

300

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Mea

n (plusmn

SE) a

bund

ance

(ind

s L-1

)

Location

Figure 43 Mean (plusmnSE) abundances (individuals L-1) of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

242 Species richness

A total of 19 taxa were identified from the benthic samples at JervoisndashWellington Mean richness was lowest at the upstream channel site (333 plusmn 038 taxa) and highest at discharge point near the bank (733plusmn084 taxa Figure 44) No significant differences among sample locations was identified [pseudo-F215 = 071 P(perm) = 0548] nor between bank and channel habitats [pseudo-F116 = 390 P(perm) = 0053]

9

8

Mea

n (plusmn

SE) r

ichn

ess 7

6 5 4 3 2 1 0

USB-1 USC-1 SDP-1 DSC-2 DSB-1 DSC-1

Upstream Discharge point Downstream

Location

Figure 44 Mean (plusmnSE) richness of benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

52

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 52: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

243 Species evenness

Pieloursquos evenness diversity index was used to determine how even the abundance of each species was among the samples with higher evenness values for samples with more equal abundances of each species in a sample The evenness scores calculated ranged from 031 at USB-1 to 095 at DSC-2 (Figure 45) and were significantly different among sites [pseudo-F512 = 1268 P(perm) = 0001] The evenness values for the location of the pairs of samples did not differ significantly [pseudo-F215 = 167 P(perm) = 0224] but a significant difference between the bank and channel habitats [pseudo-F116 = 2413 P(perm) = 0001] with the bank habitats having a lower evenness score (048 plusmn 002) compared with the channel habitats (085plusmn001)

Piel

ous

even

ness

inde

x

12

10

08

06

04

02

00 USC-1 USB-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 45 Pieloursquos evenness index values for benthic invertebrates collected on 16 April 2013 at JervoisndashWellington

244 Taxonomic composition

Oligochaeta Nematoda and Crustacea were the most common taxonomic groups found in the benthic samples at each site Nematodes and Oligochaetes were the only taxa found at each sampling location (Table 8) with Oligochaetes being the single most dominant taxa consisting of 61 of the total abundance in all samples and consisting of between 28 and 86 of individuals at each site Branchiura sowerbyi a pollution tolerant species of Oligochaeta was identified from only the discharge point (both near the bank and within the main channel)

53

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 53: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

Table 8 Taxonomic list showing the abundance of each taxa identified at JervoisndashWellington on 16 April 2013

Upstream Discharge point Downstream Bank Channel Bank Channel Bank Channel

PhylumOrder Family Species USB-1 USC-1 SDP-1 DSC-1 DSB-1 DSC-2 Nematoda Nematoda spp 24 10 145 12 47 4 Platyhelminthes Temnocephalidae Temnocephala sp 2 Annelida Oligochaeta Oligochaeta spp 301 8 205 24 75 5

Branchiura sowerbyi 1 2 Mollusca Corbiculidae Cobiculina sp 1 2 Crustacea Calanoida Calanoida 6 2 3 3

Cyclopoida Cyclopoida 5 2 2 5 1 Harpacticoida Harpacticoida 1 1 Cladocera Leydigia sp 1

Ilyocryptus sp 8 8 1 Daphnia lumholtzi 1

Arachnida Pezidae Pezidae sp 2 1 Insecta Chironomidae Tanypodinae sp 3 1

Coelopynia pruinosa 1 Cladopelma sp 6 14 4 Chironomus sp 2 3 1 4 Procladius sp 2 1 1

Ceratopogonidae Ceratopogoninae sp Caenidae Tasmanocoenis tillyardi 1 2

Total abundance 348 29 388 50 136 16 Total richness 8 6 13 7 9 7

54

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 54: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

Perc

enta

ge (

) of t

otal

sam

ple

100

80

60

40

20

0

Insecta

Arachnida

Mollusca

Crustacea

Platyhelminthes

Oligochaeta

Nematoda

USB-1 USC-1 SDP-1 DSB-1 DSC-1 DSC-2

Upstream Discharge point Downstream

Location

Figure 46 Benthic taxonomic composition at each of the JervoisndashWellington sites sampled on 16 April 2013

Two Temnocephala sp (Platyhelminthes) were identified exclusively from the discharge point Temnocephala sp are common free-living flatworms which live upon freshwater crustaceans (most commonly yabbies) but are most commonly observed when water conditions are poor particularly low oxygen concentrations Temnocephala sp feed on algae and micro-organisms on the yabbies and are not harmful to the host

The ecotoxicology results have identified Cladocera to be of particularly concern for toxicity by the discharge point Three Cladocera species (each from different families) were identified from this sampling program although abundances were low for each (Table 8) Only one individual of Daphnia lumholtzi was found and was present in the upstream sites However one Leydigia sp was found at the discharge point and individuals from Ilyocrytus sp were found at all sampling locations including the discharge point

Five species of Chironomidae were found during this study with individuals from at least one species found at each location Most species were found in higher abundances in the bank samples were food and habitat is nearby but interestingly Tanypodinae were found more commonly within the main channel habitat

One member of the more sensitive EPT (Ephemeroptera Plecoptera and Trichoptera) taxa was identified from this sampling Tasmanocoenis tillyardi (Ephemeroptera Caenidae) Caenids are the least sensitive of this group of insects however so their presence was not unexpected Individuals were identified from the upstream and downstream bank samples but was absent from the bank samples near the discharge point

55

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 55: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

3 Discussion 31 Salt drains The oxidation of acid sulfate soils during the drought and the subsequent mixing with shallow groundwater during re-flooding has produced acidic water drainage in 14 salt drains across the 27 irrigation areas in the LMRIA The EPA first identified the problem in February 2011 Since its initial discovery acidity has persisted in all impacted drains and pH for the vast majority has remained below ANZECC guidelines

Monitoring of salt drains has shown persistent low pH despite decreasing acidity concentrations Alkalinity has recovered in some locations most likely as a result of localised groundwater contributions (eg Toora and Kilsby) The concentration of acidity in the drainage water is likely dependent upon the local topography current and historical land use and the extent and depth of pyrite oxidation in the soils during the drought Some difference between the sites south of Murray Bridge where irrigation is more consistent and north of Murray Bridge was noted with a more constant decrease in acidity concentrations observed in the southern sites This is most likely due to more flushing brought about by regular irrigation events pushing acidic material out of the soil profile and maintaining the groundwater levels at higher levels An elevated sulfatechloride ratio suggests that acid sulfate soils are still contributing acidity into the salt drains despite the end of the drought conditions

In addition to acidity metals such as aluminium manganese iron and arsenic are also present in the salt drains with concentrations exceeding both the aquatic ecosystems guidelines (ANZECC guidelines) and the aesthetic and health drinking water guidelines (Tables 1 and 2) Although these excessive concentrations are concerning it is important to bear in mind that metals within the drains are concentrated Plume monitoring suggests that these high concentrations are rapidly diluted once discharged

32 Plume and river water quality Despite the low pH and high metal concentrations in the drains monitoring of the mixing of the acid drainage plumes with the River Murray has detected only minor water quality impacts In general the saline plumes rapidly sink to the bottom of the river and flow downstream some distance before dispersing Salinity and minor pH changes can be observed from the discharges over 15 km downstream During low flow conditions the plumes extend further downstream Sampling in 2013 during a period of lower flow also found plumes flowing upstream at several sites By the time the acid drainage water reaches the main river channel only minor andor very sporadic exceedences of ANZECC guidelines for protection of aquatic ecosystems occurs Slight increases in median values for total iron and sulfate were observed downstream of the discharges which is consistent with acid sulfate soil impacts

33 Sediment and precipitates Sediment samples collected within the River Murray within close proximity to the Jervois-Wellington salt drain discharge point reported high concentrations of metal in particular aluminium iron and manganese (see table 3) Both upstream and downstream samples within the River reported high concentrations of metals with no clear correlation with sediments discharged from the salt drain The fate and dissolution of metal compounds in the river are discussed in greater detail in Simpson et al (2013)

34 Benthic ecology This preliminary sampling event at JervoisndashWellington has provided initial information showing that there was a considerable number of benthic invertebrates present both downstream and at the drain outfall Majority of the taxa identified were opportunistic species and the dominant two taxa Oligochaetes and Nematodes were pollution tolerant species Polluted systems are commonly observed to have high abundances of only the few species that can tolerate the conditions which can be compared to the patterns in community composition observed at JervoisndashWellington

A profound difference was observed between the bank and main channel habitat from these samples with main channel habitats having much lower macro-invertebrate abundances richness and evenness values These findings are unsurprising as the depth of the main channel limits sunlight to the benthic zone limiting the algal growth which is an important food source for invertebrates The main channel sampling location is also a distance from suitable habitat for many invertebrates Invertebrates such as Chironomidae require vegetation to reproduce No obvious difference in the

56

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 56: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

benthic community composition was observed between the sampling locations (upstream discharge and downstream) however this sampling is preliminary and further sampling is required to confirm these preliminary findings

57

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 57: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

4 Conclusion The results of this monitoring report have shown persistent acidity dissolved metals and low pH in the 14 salt drains channels of 13 irrigation areas in the LMRIA This acidic drainage water is currently being directly discharged into the River Murray a practice which is necessary to maintain the viability of the agriculture of the LMRIA

Although the acidic drainage water discharged into the river contains low pH and high concentrations of toxic metals discharge monitoring suggests rapid dilution was occurring and reducing the risk to human and environment health The dispersal of contaminated plumes is highly dependent on river flow volumes in some instances plumes have travelled upstream during periods of low flow

Sediment and precipitate sampling reported high concentrations of metals within river sediment and in sediment falling out of suspension following a discharge event Further investigation is required to determine the effect of these metals on the river ecosystem

Benthic ecology investigations identified opportunistic species and pollutant tolerant species of macro-invertabrates to be the most dominant (eg Oligochaetes and Nematodes) A profound difference in benthic communities was observed between bank and channel samples however investigations did not suggest any significant difference between upstream point of discharge and downstream samples

Given the persistent poor water quality within the LMRIA it is important that monitoring and remediation attempts continue Additional monitoring will provide greater insight in the long term

58

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 58: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acidification risks monitoring report 2011ndash12

5 Recommendations Recommendations for further investigations

bull Continued monitoring of acidic and neutral salt drains across LMRIA

bull Further understanding of the chemistry transport and fate of metal-precipitates in the salt drains and the River Murray

bull Further understanding of effect on River Murray aquatic ecosystems arising from acidic drainage water discharges

59

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3
Page 59: Lower Murray River Irrigated Area Acidification Risk · PDF fileArea (LMRIA) Acidification Project Final ... Thank you to Hon. Dean Brown and the Lower Murray Sustainable Soils ...

LMRIA acid drainge monitoring report 2013

6 References Anderson MJ Gorley RN and Clarke KR 2008 PERMANOVA+ for PRIMER Guide to Software and Statistical Methods PRIMER-E Plymouth UK

ANZECC 2000 Australian and New Zealand Guidelines for Fresh and Marine Water Quality Australian and New Zealand Environment and Conservation Council and Agriculture and Resource Management Council of Australia and New Zealand Canberra

APHA 2005 Standard Methods for the Examination of Water and Wastewater (21st edn) American Public Health Association American Water Works Association and Water Environment Federation Washington DC

Barnett S 1989 The hydrogeology of the Murray Basin in South Australia with special reference to the alluvium of the River Murray floodplain (manuscript) Masters Thesis Flinders University SA

Barnett S Cresswell D Marsden Z and Yan W 2003 Regional salt and water balances for the Lower Murray in SA Department of Water Land and Biodiversity 200327 Adelaide

EPA 2007 Regulatory monitoring and testing Groundwater sampling Environment Protection Authority Adelaide viewed 10 December 2013 wwwepasagovauxstd_filesWaterGuidelineguide_gwspdf

Leyden E Palmer D Scott P Zammit B and Mosley L 2013 Lower Murray Reclaimed Irrigation Area Acidification Risk Project Preliminary monitoring report Environment Protection Authority Adelaide

Fitzpatrick R Shand P Grocke S Baker A Simpson S Merry R Mosley L Jayalath N Raven M and Self P 2012 Assessment of re-flooded Acid Sulfate Soils in three selected areas of the Lower Murray Reclaimed Irrigation Area (LMRIA) interim draft report CSIRO Land and Water

Fitzpatrick RW Shand P Simpson S Grocke S Raven M Baker AKM Mosley LM and Self PG 2012 Assessment of re-flooded Acid Sulfate Soil environments at Long Flat Jervois Toora and Pompoota in the Lower Murray Reclaimed Irrigation Area (LMRIA) CSIRO Land and Water Science Report No 032012 220 pp

Mosley L Fleming N and Spencer J 2009 Lower Murray Reclaimed Irrigation Area (LMRIA) Rehabilitation Project environmental monitoring final report Environment Protection Authority Adelaide

Mosley L and Fleming N 2010 lsquoPollutant Loads returned to the Lower Murray River from flood-irrigated agriculturersquo Water Air and Soil Pollution 211475ndash487

NHMRCNRMMC 2011 Australian Drinking Water Guidelines Paper 6 National Water Quality Management Strategy National Health and Medical Research Council National Resource Management Ministerial Council Commonwealth of Australia Canberra

Simpson SL Fitzpatrick RW Shand P Angel BM Spadaro DA and Mosley LM 2010 lsquoClimate-driven mobilisation of acid and metals from acid sulfate soilsrsquo Marine and Freshwater Research 61129ndash138

Simpson SL Vardenega C Jarolimek CV and Angel BA 2013 Behaviour and potential impacts of acid drainage plumes being discharged to the Lower Murray Water for a Healthy Country Flagship Report CSIRO Australia

Young EG 1985 lsquoA simple drainage equation for predicting water table drawdownsrsquo Journal of Agricultural Engineering Research 31 301ndash315

60

  • Abbreviations
  • Acknowledgments
  • Summary
  • 1 Introduction
    • 11 Description of the Lower Murray Reclaimed Irrigation Area
      • 111 Regional hydro-geological setting
      • 112 Irrigation areas
      • 113 Acid sulfate soils in the LMRIA
        • 12 Sampling programs
          • 121 Salt drain sampling
          • 122 Plume sampling
          • 123 Sediment and precipitates sampling
          • 124 Benthic ecology sampling
            • 13 Water quality parameters
            • 14 Water sampling and analytical methods
              • 2 Results
                • 21 Salt drain sampling results
                  • 211 Acidity and pH
                  • 212 Alkalinity
                  • 213 Salinity
                  • 214 Metals
                  • 215 Sulfatechloride ratios
                    • 22 Plume monitoring results
                    • 321 Plume mixing dynamics
                      • 221 Summary of data in comparison to water quality guidelines
                        • 23 Sediment precipitate results
                        • 24 Benthic ecology
                          • 241 Benthic abundance
                          • 242 Species richness
                          • 243 Species evenness
                          • 244 Taxonomic composition
                              • 3 Discussion
                                • 31 Salt drains
                                • 32 Plume and river water quality
                                • 33 Sediment and precipitates
                                • 34 Benthic ecology
                                  • 4 Conclusion
                                  • 5 Recommendations
                                  • 6 References
                                  • Word Bookmarks
                                    • Title
                                    • Title2
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_1
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_2
                                    • ColumnTitle_3
                                    • ColumnTitle_3
                                    • ColumnTitle_3