Water-Quality Constituents, Dissolved-Organic … Constituents, Dissolved-Organic-Carbon Fractions,...

U.S. Department of the InteriorU.S. Geological Survey

Scientific Investigations Report 2006-5260

Prepared in cooperation with the N.J. Department of Environmental Protection

Water-Quality Constituents, Dissolved-Organic-Carbon Fractions, and Disinfection By-Product Formation in Water from Community Water-Supply Wells in New Jersey, 1998-99


By Jessica A. Hopple, Julia L. Barringer, and Janece Koleis

Prepared in cooperation with the N.J. Department of Environmental Protection


U.S. Department of the InteriorU.S. Geological Survey

U.S. Department of the InteriorDIRK KEMPTHORNE, Secretary

U.S. Geological SurveyMark D. Myers, Director

U.S. Geological Survey, Reston, Virginia 2007

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Hopple, Jessica A., Barringer, Julia L. and Koleis, Janece, 2007, Water-Quality Constituents, Dissolved-Organic-Car-bon Fractions, and Disinfection By-Product Formation in Water from Community Water-Supply Wells in New Jersey, 1998-99, U.S Geological Survey Scientific Investigations Report 2006-5260, p. 53

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iii

Contents

Abstract ...........................................................................................................................................................1Introduction.....................................................................................................................................................2

Background............................................................................................................................................2Purpose and Scope ..............................................................................................................................2Description of Study Area ...................................................................................................................2Water Use and Land Use .....................................................................................................................4Previous Investigations of Ground-Water Quality in New Jersey ................................................4

Sources of Water-Quality Constituents and Characteristics .................................................................4Volatile Organic Compounds ...............................................................................................................6Nutrients .................................................................................................................................................6Major and Minor Ions, Trace Elements, and pH ..............................................................................7Organic Carbon .....................................................................................................................................7

Methods of Investigation ..............................................................................................................................8Well Selection .......................................................................................................................................8Collection and Processing of Samples .............................................................................................8Analysis of Samples .............................................................................................................................8

Water-Quality Constituents ........................................................................................................8Organic Carbon Fractionation ...................................................................................................9Disinfection By-Product Formation ........................................................................................10Carbon Fraction Preparation for Determination of Disinfection By-Product Formation.....................................................................................................................................10Ultraviolet Absorbance Measurements .................................................................................11

Quality Assurance Program ..............................................................................................................13Quality of Source Water to Community Water-Supply Wells ...............................................................15

Volatile Organic Compounds .............................................................................................................15Nutrients ...............................................................................................................................................17 Major and Minor Ions, Trace Elements, and pH ...........................................................................18Organic Carbon ...................................................................................................................................20

Dissolved Organic Carbon Fractions and Disinfection By-Products ..................................................20Organic Carbon Fractions .................................................................................................................20Disinfection By-Products ..................................................................................................................21

Sources........................................................................................................................................21Formation of Disinfection By-Products During the Laboratory Incubation Study ..........21Formation of Disinfection By-Products in Dissolved-Organic-Carbon Fractions ...........24Laboratory Determined Formation Rates of Disinfection By-Products in Treated Water from Community Water-Supply Wells ....................................................................................26

Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types .................................................................................................................................................29

Possible Bias in Disinfection By-Product Data .............................................................................29Relations Among Disinfection By-Product Formation Potentials ...............................................30Origins of Selected Chemical Characteristics and Constituents and Their Effects on Disinfection By-Product Formation Potential ................................................................................31

iv

Dissolved Organic Carbon ........................................................................................................31Bromide .......................................................................................................................................34Iron, Manganese, and Ammonia .............................................................................................34Indicators of Disinfection By-Product Formation Potential ................................................36

Summary and Conclusions .........................................................................................................................36Acknowledgments .......................................................................................................................................37References Cited..........................................................................................................................................37Appendix 1. Quality-assurance data (blanks, replicates, and related environmental samples)

for 1) water samples and 2) chlorinated water samples from community water-supply wells, New Jersey, 1998-99 ..........................................................................................................41

Appendix 2. Constituent concentrations in, and characteristics of, water samples from 20 community water-supply wells, New Jersey, 1998-99 .............................................................47

Appendix 3. Concentrations of disinfection by-products formed in chlorinated water from seven selected community water-supply wells in New Jersey, 1998-99, during three periods of incubation .....................................................................................................................52

Figures 1-2. Maps showing— 1. Physiographic provinces of New Jersey and locations of community water-supply wells sampled during 1998-99 .............................................................................................3 2. Geologic and hydrogeologic features of New Jersey ...................................................5 3. Schematic diagram of organic compounds isolated using XA-8 and XAD-4 resin

columns during the fractionation procedure .........................................................................12 4-21. Graphs showing— 4. Concentrations of (a) methyl tert-butyl ether (MTBE), (b) trichloroethylene (TCE), (c) tetrachloroethylene (PCE), and (d) chloroform in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99 ......................................16 5. Concentrations of (a) ammonia and (b) nitrite + nitrate in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99 .......................................17 6. Concentrations of (a) chloride, (b) sodium, and (c) sulfate in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99 ..................19 7. Relation of concentrations of bromide to concentrations of chloride in water from 20 community water-supply wells in New Jersey, 1998-99 ..........................................19 8. Values of ultraviolet absorbance at 254 nanometers (UV-254) in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99 ..................20 9. Relation of trihalomethane formation potential (THMFP) to ultraviolet absorbance at 254 (UV-254) nanometers in water from 20 community water-supply wells in New Jersey, 1998-99 ...........................................................................................................24 10. Relation of concentrations of (a) bromoform (CHBr3), (b) bromodichloromethane (CHBrCl2), (c) chloroform (CHCl3), and (d) dibromochloromethane (CHBr2Cl) to specific ultraviolet absorbance (SUVA) in water from 20 community water-supply wells in New Jersey, 1998-99 ............................................................................................25 11. Relation of concentrations of (a) bromodichloromethane (CHBrCl2), (b) dibromochloromethane (CHBr2Cl), and (c) chloroform (CHCl3) in chlorinated water to concentrations of dissolved organic carbon (DOC) in source water from 20 community water-supply wells in New Jersey, 1998-99 ..........................................27

v

12. Relation of concentrations of (a) bromoform (CHBr3) and (b) dibromochloromethane (CHBr2Cl) in chlorinated water to concentrations of bromide in source water from 20 community water-supply wells in New Jersey, 1998-99 ...................................................................................................................................27 13. Trihalomethane formation over time in water from (a) well 230195, completed in a Coastal Plain aquifer, (b) well 390451, completed in a glacial aquifer, and (c) well 350083, completed in a bedrock aquifer in New Jersey, 1998-99 ................................28 14. Haloacetic acid formation over time in water from (a) well 390451, completed in a glacial aquifer, and (b) well 230195, completed in a Coastal Plain aquifer in New Jersey, 1998-99 .....................................................................................................................30 15. Trihalomethane formation potential (THMFP) in water from 20 community water- supply wells in New Jersey, by aquifer type, 1998-99 ...................................................32 16. Total haloacetic acids (HAAs) in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99 ..............................................................................33 17. Relation of total haloacetic acid concentration (HAA) to trihalomethane formation potential (THMFP) in treated water from 20 community water-supply wells in New Jersey, 1998-99 ...........................................................................................................33 18. Relation of dissolved organic carbon (DOC) concentration to trihalomethane formation potential (THMFP) in water from 20 community water-supply wells in New Jersey, 1998-99 ...........................................................................................................34 19. Relation of total haloacetic acid (HAA) concentration to ultraviolet absorbance at 254 nanometers (UV-254) in water from 20 community water-supply wells in New Jersey, 1998-99 ...........................................................................................................34 20. Concentrations of bromide in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99 ........................................................................................35 21. Relation of concentrations of dissolved organic carbon (DOC) to concentrations of ammonia in water from 20 community water-supply wells in New Jersey Coastal Plain aquifers, 1998-99 ........................................................................................................35

Tables 1. Maximum contaminant levels and maximum residual levels goals for the Disinfection

By-Product Rule. ...........................................................................................................................2 2. Selected New Jersey State Primary and Secondary Drinking Water Standards .............6 3. Well identification, aquifer information, and well-construction data for 20 community

water-supply wells, New Jersey ................................................................................................9 4. Water-quality characteristics and constituents, analytical or measurement methods,

and analyzing laboratory for samples from 20 community water-supply wells, New Jersey, 1998-99 ............................................................................................................................10

5. Minimum reporting limits for water-quality constituents ....................................................11 6. Summary of organic carbon fractions isolated using XAD-8 and XAD-4 resin columns

during fractionation procedure ................................................................................................13 7. Summary of types, purpose, and results of quality-assurance and quality-control

analyses for water-quality samples from 20 community water-supply wells, New Jersey, 1998-99 ............................................................................................................................14

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8. Concentrations of dissolved organic carbon fractions in water samples from 20 community water-supply wells, New Jersey, 1998-99 .........................................................22

9. Concentrations of trihalomethanes in laboratory chlorinated ground-water samples from 20 community water-supply wells, New Jersey, 1998-99, following a 7-day incubation period ........................................................................................................................23

10. Measurements of ultraviolet absorbance at 254 nanometers (UV-254) and calculations of specific ultraviolet absorbance (SUVA) for water from 20 community water-supply wells, New Jersey, 1998-99 .......................................................................................................26

11. Concentrations of haloacetic acids in chlorinated ground-water samples from 20 community water-supply wells, New Jersey, 1998-99, following a 7-day incubation period ............................................................................................................................................29

12. Concentrations of haloacetonitriles in chlorinated ground-water samples from 20 community water-supply wells, New Jersey, 1998-99, following a 7-day incubation period ............................................................................................................................................30

13. Concentrations of disinfection by-products in dissolved-organic-matter fractions in water samples from 20 community water-supply wells, New Jersey, 1998-99 ................31

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Conversion Factors and DatumMultiply By To obtain

Length

centimeter (cm) 0.3937 inch (in.)

millimeter (mm) 0.03937 inch (in.)

meter (m) 3.281 foot (ft)

Volume

cubic meter (m3) 6.290 barrel (petroleum, 1 barrel = 42 gal)

liter (L) 33.82 ounce, fluid (fl. oz)

liter (L) 2.113 pint (pt)

liter (L) 1.057 quart (qt)

liter (L) 0.2642 gallon (gal)

liter (L) 61.02 cubic inch (in3)

Temperature in degrees Celsius (°C) may be converted to degrees Fahrenheit (°F) as follows:

°F=(1.8×°C)+32

Vertical coordinate information is referenced to the “The National Geodetic Vertical Datum of 1929: (NGVD 1929).”

Altitude, as used in this report, refers to distance above the vertical datum.

Specific conductance is given in microsiemens per centimeter at 25 degrees Celsius (µS/cm at 25 °C).

Concentrations of chemical constituents in water are given either in milligrams per liter (mg/L) or micrograms per liter (µg/L).


By Jessica A. Hopple, Julia L. Barringer, and Janece Koleis

Abstract Water samples were collected from 20 community water-

supply wells in New Jersey to assess the chemical quality of the water before and after chlorination, to characterize the types of organic carbon present, and to determine the disinfec-tion by-product formation potential. Water from the selected wells previously had been shown to contain concentrations of dissolved organic carbon (DOC) that were greater than 0.2 mg/L. Of the selected wells, five are completed in unconfined (or semi-confined) glacial-sediment aquifers of the Piedmont and Highlands (New England) Physiographic Provinces, five are completed in unconfined bedrock aquifers of the Piedmont Physiographic Province, and ten are completed in unconsoli-dated sediments of the Coastal Plain Physiographic Province. Four of the ten wells in the Coastal Plain are completed in confined parts of the aquifers; the other six are in unconfined aquifers.

One or more volatile organic compounds (VOCs) were detected in untreated water from all of the 16 wells in uncon-fined aquifers, some at concentrations greater than maximum contaminant levels. Those compounds detected included aliphatic compounds such as trichloroethylene and 1,1,1-tri-chloroethane, aromatic compounds such as benzene, the triha-lomethane compound, chloroform, and the gasoline additive methyl tert-butyl ether (MTBE).

Concentrations of sodium and chloride in water from one well in a bedrock aquifer and sulfate in water from another exceeded New Jersey secondary standards for drinking water. The source of the sulfate was geologic materials, but the sodium and chloride probably were derived from human inputs.

DOC fractions were separated by passing water samples through XAD resin columns to determine hydrophobic frac-tions from hydrophilic fractions. Concentrations of hydropho-bic acids were slightly lower than those of combined hydro-philic acids, neutral compounds, and low molecular weight compounds in most samples.

Water samples from the 20 wells were adjusted to a pH of 7, dosed with sodium hypochlorite, and incubated for 168 hours (seven days) at 25 °C to form disinfection by-products (DBPs). Concentrations of the DBPs—trihalomethanes, halo-acetic acids, haloacetonitriles, and chlorate—were measured. Concentrations of these compounds, with few exceptions, were higher in water from Coastal Plain wells than from wells in glacial and bedrock aquifers.

The organic-carbon fractions were dosed with sodium hypochlorite, incubated for 168 hours at 25 ºC, and analyzed for trihalomethanes, haloacetic acids, haloacetonitriles, and chlorate. Concentrations of trihalomethanes and haloacetic acids were higher in most of the hydrophobic organic-acid fractions than in the hydrophilic fractions, with the highest concentrations in samples from Coastal Plain aquifers. Traces of haloacetonitriles were measured, mostly in the hydrophilic fraction.

The aromaticity of the precursor DOC, as estimated by measurements of the absorbance of ultraviolet light at 254 nanometers, apparently is a factor in the DBP forma-tion potentials determined, as aromaticity was greater in the samples that developed high concentrations of DBPs. VOCs may have contributed to the organic carbon present in some of the samples, but much of the DOC present in water from the 20 wells appeared to be natural in origin. The sediments of the Coastal Plain aquifers, in particular, contain substantial amounts of organic matter, which contribute ammonia, organic nitrogen, and aromatic DOC compounds to the ground water. Thus, the geologic characteristics of the aquifers appear to be a major factor in the potential for ground water to form DBPs when chlorinated.

Introduction

Background

The chemical quality of a ground-water source is a primary concern when that source is used for public and domestic supply. Regulations enacted by the U.S. Environ-mental Protection Agency (USEPA) (U.S. Environmental Protection Agency, 1994) and the New Jersey Department of Environmental Protection (NJDEP) (New Jersey Depart-ment of Environmental Protection, 1997) require community water-supply purveyors to monitor ground water for a variety of contaminants that include radionuclides, trace elements, and volatile organic compounds (VOCs) (for example, Louis and others, 1994). The U.S. Geological Survey (USGS), in cooperation with NJDEP, has participated in several research projects investigating the relation of the chemical quality of water to hydrogeology and to land use. These studies have been designed to assess the vulnerability of the source waters of community water-supply wells to contamination by pes-ticides, radionuclides, VOCs, and compounds that form as a result of disinfection of drinking water, known as disinfection by-products (DBPs).

The results of the vulnerability studies can be used by water-supply managers to evaluate strategies for monitoring the quality of water in community water-supply wells. Moni-toring requirements for certain constituents could be waived or reduced for wells that are not vulnerable to human or natural sources of contamination.

New regulations adopted by USEPA, with respect to the Disinfection By-Products Rule (DBPR) and the Infor-mation Collection Rule (ICR), increased the requirements for water purveyors to collect detailed information on both source waters and treated waters. The DBPR, which sets maximum contaminant levels (MCLs) for trihalomethanes (THMs), haloacetic acids (HAAs), bromate, and chlorite, and maximum residual disinfection concentrations for chlorine, chloramines, and chlorine dioxide (table 1), was established in 1994 (U.S. Environmental Protection Agency, 1994). Stage 1 of the DBPR took effect in November 1998 when the MCL for THMs was lowered from 100 µg/L to 80 µg/L and an MCL for HAAs at 60 µg/L was established.

The ICR requires utilities that get their water from ground-water sources and that serve populations greater than 50,000 to start monitoring for DBPs and microbial contaminants. A method is needed to determine whether the vulnerability of water from community water-supply wells to contamination from DBPs can be predicted on the basis of source-water chemical constituents derived from human or natural inputs. This method could be used by water mangers to assess the need for chemical analyses of water supplies that may be of low vulnerability. This vulnerability study was conducted by USGS, in cooperation with NJDEP, to determine

the quality of source water to 20 community supply wells and to investigate a method for predicting the formation of DBPs.

Purpose and Scope

This report describes a study to determine (1) whether the quality of source water to 20 community water-supply wells across New Jersey was compromised by contaminants, and (2) whether the vulnerability of water from community water-supply wells to contamination by the formation of DBPs can be predicted on the basis of hydrogeologic and water-quality indicators. The quality of water withdrawn from the supply wells was determined and is assessed in light of contaminant inputs to ground water from natural sources and human activ-ity. As possible precursors to DBP formation, various types of organic carbon are identified and their relation to the potential for DBP formation in water from confined and unconfined aquifers is evaluated. Water-quality and quality-assurance data are presented and discussed.

Description of Study Area

New Jersey has a humid, temperate climate; average annual precipitation is about 45 inches. The State contains parts of four major physiographic regions or provinces known as the Coastal Plain, the Piedmont, the Highlands (otherwise known as the New England Province), and the Valley and Ridge provinces (fig. 1). Within these provinces, different geologic settings create a variety of aquifer types.

Aquifers consisting of unconsolidated sediments underlie most of the Coastal Plain Physiographic Province in southern New Jersey and are present in glacial deposits in northern New Jersey. The aquifers of the Coastal Plain vary in areal extent and thickness and consist of permeable units of sand and gravel that are separated from one another by less perme-able confining units of silt and clay. Sediments of the predomi-

Table 1. Maximum contaminant levels and maximum residual levels goals for the Disinfection By-Product Rule. 1

[MCL, maximum contaminant level; MRLG, maximum residual levels goal; µg/L, micrograms per liter; mg/L, milligrams per liter]

Constituent/Constituent group Concentration

Disinfection by-products MCLTrihalomethanes 80 µg/LHaloacetic acids 60 µg/LBromate 10 µg/LChlorite 1.0 µg/L

Residual disinfectant MRLGChlorine 4 mg/LChloramines 4 mg/LChlorine dioxide 0.8 mg/L

1 U.S. Environmental Protection Agency, 1994

� Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

150207

150276

090136

070368

070177

050039

010039

010600

291264

230195

210402

130098

030301

030460

390451

270182270155

270147

270080

350083

COASTAL PLAIN

PIEDMONT

NEW ENGLAND (HIGHLANDS)

VALLEY AND RID

GE

EXPLANATION

Glacial

Coastal Plain, unconfined

Coastal Plain, confined

Bedrock

291264 WELL LOCATION AND NUMBER--Color identifies type of aquifer:

7475

41

40

39

0 20 MILES10

0 30 KILOMETERS15

Figure 1. Physiographic provinces of New Jersey and locations of community water-supply wells sampled during 1998-99.

Introduction �

nantly unconfined Kirkwood-Cohansey aquifer system crop out over 3,000 mi2 of the Coastal Plain. The aquifer system is confined on the Cape May peninsula at the southern tip of the State and near the Atlantic coastline (Zapecza, 1989). Five other major aquifers or aquifer systems composed of uncon-solidated sediments underlie the Kirkwood-Cohansey aquifer system; these are mostly confined except in areas along the western and northern parts of the Coastal Plain, where their sediments are at land surface (fig. 2). The glacial aquifers typically are composed of valley-fill sediments, are mostly unconfined, and generally are present north of the terminal moraine of the last (Wisconsin) period of glaciation. Bedrock aquifers, which are mostly unconfined, occur in fractured shales and sandstones in the Piedmont Province, in weathered and fractured crystalline rocks of the Highlands Province, and in porous limestones and dolomites, and fractured conglomer-ates, sandstones, siltstones, and shales of the Valley and Ridge Province.

Water Use and Land Use

Freshwater use in New Jersey, the most populous of the 50 United States, currently is estimated at about 2,200 mil-lion gallons per day. About 27 percent of this volume comes from ground water, of which about 67 percent is provided by community water-supply wells (John Nawyn, U.S. Geological Survey, written commun., 2003).

The quality of the water provided by wells completed in unconfined aquifers can be affected by contaminants introduced at or near the land surface by human activities. Confined aquifers, which can contain water that entered as recharge hundreds to thousands of years ago, are less vulner-able to this type of contamination. Water in both aquifer types, however, can be affected by naturally occurring contaminants released by the aquifer materials.

Agricultural, residential, and urban developments consti-tute the predominant uses of land in New Jersey. A substantial increase in residential development since World War II has occurred largely, although not entirely, at the expense of agri-cultural land. Land development brings with it the potential for contamination of ground water. Agricultural practices can contribute contaminants through use of fertilizers and pesti-cides; residential, commercial, and industrial activities can contribute contaminants through the use of septic tanks and releases of fuels, solvents, and other chemicals. Large tracts of undeveloped land remain, primarily in southern New Jersey. Ground-water quality is less likely to be adversely affected in these areas than in developed parts of the State, unless ground-water flow moves contaminants from parts of the aquifers underlying developed land to those parts underlying adjacent undeveloped areas.

Previous Investigations of Ground-Water Quality in New Jersey

A summary of the quality of New Jersey ground water and a discussion of the vulnerability of water supplies to contamination is presented in Ayers and Pustay (1988) as part of the U.S. Geological Survey National Water Summary. Pesticides and nutrients were measured in water from 90 com-munity water-supply wells during 1994-95 (Clawges and oth-ers, 1998). The occurrence of nitrates, pesticides, and VOCs in ground water in southern New Jersey was determined by Stackelberg and others (1997). THM formation potential, how-ever, has not been studied previously in New Jersey ground waters, but an investigation of the formation potential in water in Kansas aquifers has been reported by Miller and others (1990).

Sources of Water-Quality Constituents and Characteristics

The concentrations of chemical constituents in ground water are related to the sources of the constituents and to the physical, biological, and chemical processes that have occurred along ground-water flow paths. Some sources of con-stituents occur naturally; others result from human activities. Natural sources of constituents include those in precipitation entering aquifers as recharge, minerals and organic matter in soils, and the minerals and organic matter that compose the aquifer matrix. In some hydrogeologic settings, surface water also can provide recharge and can contribute constituents to ground water. Human-induced sources from the land surface and subsurface include applications of agricultural chemi-cals, and disposal of industrial chemicals and other wastes. Natural processes affect the concentrations of both natural and human-induced constituents—these processes include biological degradation of organic matter, mineral dissolution and precipitation, ion exchange, oxidation-reduction reactions, adsorption and desorption of solutes, and generation/coagula-tion of colloids.

Because certain constituents in drinking water are known to pose human health hazards, standards have been set for these constituents by the USEPA and by State agencies such as NJDEP (U.S. Environmental Protection Agency, 2001; New Jersey Department of Environmental Protection, 1997). The National Primary Drinking Water Regulations set either a maximum contaminant level (MCL), which is the maxi-mum permissible level of a contaminant in water delivered to a public system, or an Action Level (AL), the concentration at which remedial action must take place. A health advisory level (HAL) has been promulgated for a few constituents; this is a nonregulatory estimate of the concentration that, over a lifetime of exposure, would result in no known or anticipated health effect. The standards set by NJDEP are, in some cases,


7475

41

40

39

0 20 MILES10

0 30 KILOMETERS15

130098

030301

030460

390451

350083

291264

270182270155

270147

270080

230195

210402

150207

150276

070368070177

050039

090136

010039

010600

Glacial

Coastal Plain, unconfined

Coastal Plain, confined

Bedrock

291264WELL LOCATION AND NUMBER--Color identifies type of aquifer:

EXPLANATION

GEOLOGIC UNITS

Crystalline Rocks

Passaic Formation

Glacial sediment

Extent of Terminal Moraine

Other bedrock Formations

Boonton Formation

Stockton Formation

Other unconsolidated sedimentary Formations

Potomac, Raritan, and Magothy Formations

Mt. Laurel and Wenonah Formations

Kirkwood and Cohansey Formations

Holocene age sediments of the Coastal Plain

Figure �. Geologic and hydrogeologic features of New Jersey.

Sources of Water-Quality Constituents and Characteristics �

more stringent than the Federal standards and include second-ary maximum contaminant levels (SMCLs), which are not based on health issues, but on the aesthetic issues of smell, taste, foaming, staining, and corrosiveness to plumbing. The NJDEP drinking-water standards for the constituents analyzed during this investigation are listed in table 2.

Volatile Organic Compounds

VOCs are a class of organic compounds, primarily halogenated aliphatic and monocyclic aromatic hydrocarbons, that are characterized by high vapor pressures; that is, they volatilize easily, and they are highly soluble (Smith and others, 1988).

VOCs have a multitude of uses in modern society. VOCs are present in fuels and the exhaust from their combustion. They are found in common household products such as air fresheners, perfumes, bathroom deodorants, cleaning and pol-ishing products, paints, solvents, adhesives, and ink. They also are widely used in industrial applications as degreasers and refrigerants, in the dry-cleaning industry, in the manufacture of pharmaceutical products and plastics, in a process used to decaffeinate coffee, and in agricultural applications as active and inactive components of pesticides and fumigants (Bloe-

men and Burn, 1993; Smith and others, 1988; Verschueren, 1983).

Some VOCs occur naturally; the ethylene emitted as gas by ripening fruit is an example. Of the trihalomethanes, chlo-roform has been shown to form naturally (Hoekstra and others 1998). Nevertheless, at the levels at which contamination of soils and water occurs, the sources of VOCs are derived from human activities. VOC use, improper storage, and (or) disposal at the land surface or in the subsurface can lead to contamination of underlying aquifer systems, and, in some instances, to contamination of water tapped by community water-supply wells.

Many VOCs are toxic and (or) carcinogenic; conse-quently, MCLs have been developed for these compounds. MCLs range from 1 to 1,000 µg/L, depending on the toxicity of the compound (table 2) (New Jersey Department of Envi-ronmental Protection, 1997).

Nutrients

Nutrients, which include nitrogen and phosphorus and their compounds, are essential for animal and plant growth. Natural sources of nutrients include wet and dry atmospheric deposition, biologically-mediated fixation, and the dissolution

Table �. Selected New Jersey State Primary and Secondary Drinking Water Standards.

[MCL, maximum contaminant level; SMCL, secondary MCL (recommended upper limit or optimum range); µg/L, micrograms per liter; mg/L, milligrams per liter; prefixes in parentheses ( ) are alternate or additional prefixes]

Constituent Standard (units) Constituent or characteristic Standard (units)

Volatile Organic Compounds MCL (µg/L) Volatile Organic Compounds MCL (µg/L)Benzene 1 Trichloroethylene 1Carbon Tetrachloride 2 Vinyl chloride 2(meta) 1,3-Dichlorobenzene 600 Xylenes [total] 1,000(ortho) 1,2-Dichlorobenzene 600 Trihalomethanes [total]1 80(para) 1,4-Dichlorobenzene 75 Inorganic Constituents MCL (mg/L)1,1-Dichloroethane 50 Fluoride 41,2-Dichloroethane 2 Nitrate [as nitrogen] 101,1-Dichloroethylene 2 Nitrite [as nitrogen] 1cis-1,2-Dichloroethylene 70 Characteristics SMCLtrans-1,2-Dichloroethylene 100 pH 6.5-8.5 optimum1,2-Dichloropropane 5 Inorganic Constituents SMCL (mg/L)Ethylbenzene 700 Chloride 250Methyl tert-Butyl Ether 70 Fluoride 2Methylene Chloride 3 Hardness2 [as CaCO3] 250(Mono) Chlorobenzene 50 Iron 0.3Styrene 100 Manganese 0.05Tetrachloroethylene 1 Sodium 50Toluene 1,000 Sulfate 2501,1,1-Trichloroethane 30 Total dissolved solids 500

1 Total trihalomethanes are the sum of concentrations of bromoform, bromodichloromethane, dibromochloromethane, and chloroform.2 Hardness is the sum of milliequivalents per liter of calcium and magnesium, and is multiplied by 50 to express as CaCO3. (New Jersey Depart-

ment of Environmental Protection, 1997)


or precipitation of organic matter. Anthropogenic point sources of nitrogen and phosphorus, as elements or compounds, include municipal and industrial discharges and effluent from individual septic systems or cess pools. Anthropogenic nonpoint sources include leaching of domestic and agricultural fertilizers, manure deposited on or applied to the land sur-face, and effluent from leaking sewer lines or groups of septic systems.

Ammonia is generally the predominant form of nitro-gen in agricultural fertilizers and septic-system effluents. Ammonia (or ammonium ion) is volatile and, therefore, can be transported through the atmosphere and deposited in wet or dry form. In the presence of oxygen it is converted to nitrite, then to nitrate through a microbiologically mediated process called nitrification. The ammonium ion also adsorbs to miner-als (Hem, 1992), and thus is retarded as it moves through soils and aquifer materials. Consequently, because of oxidation (nitrification) and (or) retardation through adsorption, concen-trations of ammonia in ground water are usually low, unless the geochemical environment of the aquifer is reducing (little or no oxygen). Furthermore, because nitrite quickly oxidizes to nitrate, nitrite also generally remains at low concentrations in both surface and ground water. Nitrate is present in some fertilizers and enters the atmosphere from auto exhaust and industrial smokestacks. Consequently, infiltration of precipita-tion can be a source of ammonia, nitrite, and nitrate ions to ground water. Nitrate from fertilizer, and animal (and human) wastes leaches easily through soils (Hem, 1992); as a result, concentrations in ground water can exceed 10 mg/L, particu-larly in agricultural areas. In reducing parts of an aquifer, however, nitrate may not be detected, whereas ammonia (and perhaps nitrite) are likely to be detected.

An MCL (10 mg/L as N) has been promulgated for nitrate in drinking water because high concentrations can cause the potentially fatal blood disorder called methemoglobinemia, or “blue baby disease;” this primarily affects children under 6 months of age. High concentrations of nitrite can cause the same disorder. As a result, an MCL (1 mg/L as N) has been developed for nitrite as well (table 2). No MCL for ammonia has been developed.

Phosphorus is an essential element in metabolism. Organic phosphorus species synthesized by plants and animals constitute a significant fraction of phosphorus in many natural waters (Hem, 1992), where it is usually found in concentra-tions less than a few tenths of a part per million. Large quanti-ties of phosphorus are introduced to the environment through the use of fertilizers; because phosphorus binds strongly to fine-grained soils and organic material, phosphate from fertilizer or organic wastes typically does not leach easily into ground water.

Major and Minor Ions, Trace Elements, and pH

Major ions (calcium, magnesium, sodium, potassium, chloride, and sulfate) and trace elements (arsenic and metals

such as iron and manganese) are contributed to ground water mainly through weathering processes that result in dissolu-tion of minerals in soils, sediments, and bedrock. Major ions such as calcium, magnesium, potassium, chloride, and sulfate also can be contributed to ground water by land application of agricultural chemicals. Wastewater discharges contribute major ions, particularly sodium, chloride, bicarbonate, and sulfate, and trace elements. In some areas, use of road salt during winter can lead to increases in sodium and chloride in ground water.

There also are inputs to the land surface from atmo-spheric deposition, both wet (precipitation) and dry deposi-tion. Mineral sources of chloride, for example, generally are not abundant, but precipitation can be an important source of this ion; concentrations of sodium and calcium also tend to be high in precipitation in New Jersey (Graedel and Reiss, 1985). Because chloride tends not to adsorb to soil materials, it can move easily from the land surface to the water table.

Bromide and fluoride typically are present in minor amounts in ground water. Bromide is contributed primarily by precipitation and can be of natural origin (for example, salt spray, which also contributes chloride) or from anthropogenic sources. Fluoride typically is derived from dissolution of min-erals in the aquifer matrix (Hem, 1992).

Most of the trace elements in ground water are metal and metalloid ions such as aluminum, arsenic, copper, lead, iron, and manganese. Minerals in the aquifer matrix typically contribute metals such as aluminum, iron, and manganese; other metals and metalloids also can be derived from mineral sources. Industrial releases to the land surface and subsurface, also pesticide use, can contribute metallic and metalloid trace elements, sometimes at high concentrations, to ground water (Hem, 1992). Metals emitted by industrial activities also are deposited from the atmosphere to the land surface. Manga-nese, for example, is present mostly in particulate form, and is deposited near its sources (Adriano, 1986). Acidic precipi-tation can leach metals from soils, but some, such as lead, with an affinity for soil organic matter and clays, tend to be adsorbed (Adriano, 1986) and thus retained in the soils.

Ground-water pH (hydrogen-ion activity) is controlled by a variety of chemical reactions that consume or produce hydrogen ions. These reactions include dissociation of water, interactions between water and gases, dissolution of miner-als, hydrolysis of metal ions, and oxidation/reduction (redox) reactions (Hem, 1992). These reactions take place in the soil, between recharge waters and soil constituents, and in the aqui-fer, between water and aquifer materials. Insofar as chemicals of anthropogenic origin can be involved in some of these reac-tions, the pH of ground water, on a local scale, can be affected by human activities.

Organic Carbon

Natural sources of organic carbon in ground water include (1) decomposing plants and other organic matter that

Sources of Water-Quality Constituents and Characteristics �

infiltrate in recharge from soils, or are carried in recharge by surface waters to ground water, and (2) altered (in some cases, fossilized) remnants of organic matter, such as lignite and kerogen, in the geologic materials that compose aquifers (Thurman, 1985). Anthropogenic sources of organic carbon include septic-system effluent, animal feedlots, and compost-ing facilities. Decomposing VOCs also can contribute organic carbon to ground water.

Organic carbon can be measured as total organic car-bon (TOC), which includes particulate and dissolved organic carbon (DOC), which is defined as the organic carbon that passes through a 0.45 µm pore-size silver or 0.7 µm pore-size glass-fiber filter. DOC has been considered the chemically reactive fraction and is composed mostly of humic substances and hydrophilic acids (Thurman, 1985). Nevertheless, because colloids are increasingly found to be involved in contami-nant transport in aquifers, organic carbon (humic substances, lignin) as colloids or as coatings on inorganic colloids can play a role in both soil and ground-water contaminant mobility (McCarthy and Zachara, 1989; Kretzschmar and others, 1995). Consequently, determinations of TOC can be useful to the understanding of transport of adsorbed constituents in ground water.

Methods of Investigation

Well Selection

Wells to be sampled were selected on the basis of previ-ous water-quality results reported in the USGS National Water Information System database. An emphasis was placed on wells completed in unconfined aquifers because the vulner-ability of those wells to human-induced contaminants was considered high relative to that of wells completed in confined aquifers or in confined parts of aquifers. Existing water-qual-ity data for the chosen wells indicated that those in the Coastal Plain generally yielded water containing higher concentrations of DOC, and thus, the water could have a higher potential for forming DBPs than water from the other physiographic provinces. Wells yielding water with low DOC concentrations (less than 0.2 mg/L) were not chosen for sampling because carbon-fractionation and analytical problems were anticipated for such samples. Locations of the selected wells are shown in figure 1, and well-construction data are presented in table 3.

Collection and Processing of Samples

Water samples were collected from the 20 selected wells during 1998–99. Sampler tubing and connectors were cleaned following procedures described by Koterba and others (1995); DOC filter units were cleaned in a sonifier using three suc-cessive rinses of organic-free de-ionized water. Ground-water

samples were collected at the wellhead prior to any disinfec-tion or other treatment to represent the quality of the water from the aquifer before treatment. Flow from the wellhead was routed through Teflon tubing into an instrumented flow-through cell in which water temperature, pH, specific conductance, and dissolved oxygen (DO) were measured continuously. These measurements were recorded every 3 to 5 minutes until differences in values for three or more succes-sive measurements fell within the following criteria: tempera-ture, 0.2 ºC; 0.05 pH units; 5 percent of specific conductance values less than or equal to 100 µS/cm (microsiemens per centimeter) or 3 percent of specific conductance values greater than 100 µS/cm; and DO, 0.3 mg/L. This approach ensured the collection of fresh water from the aquifer rather than stand-ing water from the well casing. Upon stabilization of the field measurements, the sample flow was routed into a polyethylene sample-collection chamber in order to minimize exposure to air-borne contaminants.

Samples for VOC analysis were collected by filling the sample vial from the bottom with a Teflon tube and allowing the vial to overflow before capping. Samples collected for analysis for total organic carbon (TOC), DOC, and ultraviolet light absorbance at 254 nanometers (UV-254), and for organic-carbon fractionation were collected directly into bottles with no overflow; of these, samples for DOC analysis and frac-tionation were filtered through 47-mm-diameter, 0.45-µm pore-size silver filters. Samples for analysis of dissolved major ions, trace elements, and nutrients, were passed through 0.45-µm-pore-size capsule filters, which were conditioned with 1 liter (L) of native water prior to sample collection. Samples for analysis of major cations and trace elements were preserved with nitric acid according to USGS protocols. Alkalinity was measured in the field by incremental titration (Koterba and others, 1995).

In addition to the samples of untreated water for analysis of water-quality constituents, three 1-L water samples were collected from each well for determination of DBP formation potential. Additional 1-L samples were collected from selected wells for determination of the rate of DBP formation. All samples for laboratory analysis were chilled on ice immedi-ately following collection and were shipped overnight to the analyzing laboratories.

Analysis of Samples

Water-Quality ConstituentsThe water samples were analyzed at four laboratories

(table 4). Samples for major ions, trace elements, nutrients, and VOCs were analyzed at the USGS National Water Qual-ity Laboratory (NWQL) in Arvada, Colorado. Samples were analyzed for DOC and TOC at NWQL and the USGS National Research laboratory, Boulder Colorado. Methods used are described by Connor and others (1998); Brenton and Arnett (1993); and Fishman and Friedman (1989). Measurements of

8 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

UV-254 were made at the National Research laboratory in Boulder and at the USGS New Jersey Water Science Cen-ter laboratory in West Trenton, New Jersey, using Standard Method 5910 (Eaton and others, 1995). Incubation studies and DBP analysis using USEPA Standard Methods (table 4) were performed at the Environmental Health Laboratory (EHL), in South Bend, Indiana. The minimum reporting limit (MRL), which is the minimum concentration of an analyte that can be reliably measured by the laboratory using a given analytical method, is shown for each constituent in table 5. (For VOCs, some detections are reported as estimated concentrations below an MRL of 0.2 µg/L, however, and the actual estimated values do not appear in data tables in appendix 2.)

Organic Carbon FractionationBecause organic acids are absorbed in the proton-

ated form (Thurman, 1985), DOC samples were acidified, using hydrochloric acid (HCl), to a pH between 1.90 and

1.99. Columns containing non-ionic acrylic-ester copoly-mer resins XAD-8 and XAD-4 were connected in series and used to extract hydrophobic and hydrophilic carbon frac-tions in selected samples (fig. 3). Hydrophobic organic acids were extracted onto the XAD-8 resin in the first column and retrieved by back-eluting with 0.1 N sodium hydroxide (NaOH) for all samples. The hydrophilic organic acids, which passed through the first column, were retained on the XAD-4 resin, and, for six samples, were retrieved by again back-elut-ing with NaOH. Both eluates were immediately acidified with HCl to a pH between 1.90 and 1.99 to prevent organic carbon degradation (Aiken and others, 1992). The low-molecular-weight hydrophilic (transphilic) compounds passed through both columns.

Both the hydrophobic organic acids and the hydrophilic organic acids then were further concentrated on the XAD-8 and XAD-4 columns, respectively. The columns were desalted with deionized water and the samples back-eluted with NaOH onto separate cation-exchange resins to hydrogen-saturate the

Table �. Well identification, aquifer information, and well-construction data for 20 community water-supply wells, New Jersey.

[PRM, Potomac-Raritan-Magothy; BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; OM, organic matter; ft, feet; nd, no data; NGVD 1929, National Geodetic Vertical Datum of 1929; BLS, below land surface]

USGSwell

numberAquifer name

Aquifer type

Geologic description of aquifer materials

Land-surface

elevation (ft above

NGVD 19�9)

Total well depth

(ft BLS)

Top of open

interval (ft BLS)

Bottom of open interval

(ft BLS)

030301 Brunswick BR Red shale, some black shale 220 256 nd nd030460 Passaic BR Red shale, some black shale 32 402 46 402130098 Passaic BR Red shale, some black shale 200 551 56 551210402 Stockton BR Arkosic sandstone 50 302 nd nd350083 Passaic BR Red shale, some black shale 55 400 53 400

270080 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 520 150 88 143270147 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 190 115 85 115270155 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 330 75 60 75270182 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 180 47 30 47390451 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 95 85 50 85

050039 Middle PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 12 57 47 57070177 Lower PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 9 304 274 304070368 Lower PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 10 138 106 126150207 Lower PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 30 282 241 282230195 Oldbridge (PRM) CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 15 80 50 80291264 Kirkwood-Cohansey aquifer system CP Quartz sand/gravel/silt/clay, mica, some OM 20 77 52 72

010039 Atlantic City 800-foot sand CCP Quartz sand/gravel/silt/clay, mica, some OM 10 788 733 788010600 Atlantic City 800-foot sand CCP Quartz sand/gravel/silt/clay, mica, some OM 8 810 750 810090136 Atlantic City 800-foot sand CCP Quartz sand/gravel/silt/clay, mica, some OM 7 834 802 834150276 Upper PRM aquifer system CCP Quartz sand/gravel/silt/clay, mica, lignite (OM) 60 289 242 289

Methods of Investigation 9

samples. The desalted samples then were acidified to a pH between 1.90 and 1.99 to prevent degradation.

The hydrophobic fraction was isolated from all the hydrophilic fractions in the remainder (14) of the samples, using only the XAD-8 resin columns. For these samples, only the fractions DOC 1 (the influent solution), DOC 2 (hydro-philic organic acids), DOC 3 (hydrophobic organic acids), and DOC 4 (hydrophobic organic neutrals) are available (fig. 3). The concentration of hydrophobic neutral compounds, which are retained on the XAD-8 resin, can be calculated (table 5), as can the hydrophilic neutral compounds (fraction DOC 7), which are retained on the XAD-4 resin columns used in most of the fractionations.

These calculated concentrations should have a positive or zero value. A positive value represents the concentration of neutral compounds retained on one or the other resin columns, whereas a zero value indicates that no neutral compounds are present. A negative value indicates that leaching of organic carbon from the resin column has occurred. Such leaching is not uncommon in samples containing low (about 0.2 mg/L or less) concentrations of DOC. The full fractionation method is summarized in table 6.

Disinfection By-Product FormationUpon arrival at the analyzing laboratory, the 1-L water

samples collected for determination of DBP formation were adjusted to pH 7. The three samples from each site were dosed with sodium hypochlorite (NaOCl), one bottle each at 5, 7.5, and 10 mg/L, respectively, following EPA Standard

Methods listed in table 4. The dosed samples were incubated for 168 hours (seven days) at 25 ºC; then the samples were analyzed for residual chlorine. The sample of each set of three in which the concentration of residual chlorine was closest to 5 mg/L then was analyzed for chlorate (EPA Method 300.0) and four types of post-chlorination DBPs—THMs (EPA Method 524.2), haloacetic acids (HAAs) (EPA Method 552.2), haloacetonitriles (HANs), and chloral hydrate (EPA Method 551.1). The additional 1-L samples collected from selected wells for determination of DBP formation rate were treated as above, but concentrations of DBP were measured after 6-hour and 24-hour incubation periods.

Carbon Fraction Preparation for Determination of Disinfection By-Product Formation

The 1-L samples collected for both fractionation and determination of DBP formation were fractionated onto 20-mL columns according to the procedure described above. DOC and UV-254 were measured following each step in the fractionation procedure (described in figure 3 and table 6). Following the desalting step, these samples were acidified using phosphoric acid (H3PO4) to avoid interferences in the organic-carbon analyzer caused by the presence of HCl.

Splits of the fractionated samples were sent to EHL to be dosed with NaOCl, incubated, and analyzed for DBPs. The concentrations of NaOCl needed to obtain a residual chlorine concentration of 5 mg/L were estimated by laboratory person-nel from the amount of NaOCl with which the corresponding whole-water sample was dosed. After a 168-hour incubation

Table �. Water-quality characteristics and constituents, analytical or measurement methods, and analyzing laboratory for samples from 20 community water-supply wells, New Jersey, 1998-99.

[UV; ultraviolet; nm, nanometers; GC/MS, gas chromatography/mass spectrometry; USEPA, U.S. Environmental Protection Agency; NWQL, National Water Quality Laboratory; NJWSC; New Jersey Water Science Center laboratory; EHL, Environmental Health Laboratory]

Characteristic or constituent Instrumentation and (or) method Laboratory

Temperature Meter FieldpH Meter FieldSpecific conductance Meter FieldDissolved oxygen Meter FieldAlkalinity Incremental titration FieldVolatile organic compounds Purge and trap GC/MS NWQL Nutrients Colorimetry NWQL Major ions; trace elements Inductively coupled plasma spectroscopy NWQLTotal organic carbon Persulfate oxidation NWQL; USGS Boulder, Colo.Dissolved organic carbon UV/persulfate oxidation; persulfate oxidation NWQL; USGS Boulder, Colo.UV absorbance at 254 nm Spectrophotometry –Standard Method 59101 NJWSC; USGS Boulder, Colo.Trihalomethanes USEPA Standard Method 524.21 EHLHaloacetic acids USEPA Standard Method 552.21 EHLHaloacetonitriles USEPA Standard Method 551.11 EHLChlorate USEPA Standard Method 300.01 EHLChloral hydrate USEPA Standard Method 551.11 EHL

1 Eaton and others, 1995


period at 25 ºC, the fractions were analyzed for THMs, HAAs, HANs, and total chlorine residual.

Ultraviolet Absorbance MeasurementsOrganic constituents absorb ultraviolet (UV) light in

proportion to their concentration. Measurements of UV-254 are directly related to concentration and the aromaticity of a compound (Eaton and others, 1995). Specific UV absorbance, which is UV-254 normalized to the concentration of DOC (SUVA = UV-254/DOC x 100), relates to the aromaticity. Water samples for UV-254 analysis typically are filtered in

order to avoid absorption interferences by particulate mat-ter. Other interferences in UV absorption may arise from the presence of large concentrations of ferrous iron, nitrate, nitrite, bromide, chlorate, chlorite, and chloramines, as noted in EPA Method 415.3 (Eaton and others, 1995). Consequently, sam-ples with high iron concentrations (> 1,000 µg/L) were filtered twice to remove any iron-bearing particulates. Measurements are made, using a spectrophotometer, by placing an aliquot of sample in a quartz glass cuvette and measuring the absorbance at 254 nanometers. The absorbance value is compared with a standard curve developed by determining absorbance of solu-tions of known, standard concentration.

Table �. Minimum reporting limits for water-quality constituents.

[MRL, minimum reporting limit; mg/L, milligrams per liter; µg/L, micrograms per liter; N, nitrogen; P, phosphorus; DBPs, disin-fection by-products; EHL, Environmental Health Laboratory]

Constituent MRL Constituent MRL

Major ions and trace elements Volatile organic compounds -- continued

Calcium 0.2 mg/L trans-1,2-Dichloroethylene 0.2 µg/L Magnesium 0.004 mg/L Dichloromethane 0.2 µg/L Potassium 0.1 mg/L Dichloropropane 0.2 µg/L Sodium 0.1 mg/L Ethylbenzene 0.2 µg/L Chloride 0.1 mg/L Methyl tert-butyl ether 0.1 µg/L Sulfate 0.1 mg/L Styrene 0.2 µg/L Bromide 0.01 mg/L Tetrachloroethylene 0.2 µg/L Fluoride 0.1 mg/L Tetrachloromethane 0.2 µg/L Iron 10 µg/L Toluene 0.2 µg/L Manganese 4 µg/L 1,1,1-Trichloroethane 0.2 µg/L Silica 0.1 mg/L Trichloroethylene 0.2 µg/L

Nutrients Trichlorofluoromethane 0.2 µg/L Ammonia (as N) 0.02 mg/L 1,1,2-Trichlorotrifluoroethane 0.2 µg/L Ammonia + organic N 0.1 mg/L Vinyl chloride 0.2 µg/L Nitrite (as N) 0.01 mg/L Xylene 0.2 µg/L Nitrite + nitrate (as N) 0.05 mg/L DBPs (analyzed by EHL) Orthophosphorus (as P) 0.01 mg/L Trihalomethanes

Organic carbon Bromoform 0.1 µg/L Dissolved organic carbon 0.1 mg/L Bromodichloromethane 0.1 µg/L Total organic carbon 0.1 mg/L Chloroform 0.1 µg/L

Volatile organic compounds Dibromochloromethane 0.1 µg/L Benzene 0.2 µg/L Haloacetic acids Bromodichloromethane 0.2 µg/L Bromochloroacetic acid 1.0 µg/L Bromoform 0.2 µg/L Dibromoacetic acid 1.0 µg/L Chlorobenzene 0.2 µg/L Dichloroacetic acid 1.0 µg/L Chloroform 0.2 µg/L Monochloroacetic acid 1.0 µg/L Dibromochloromethane 0.2 µg/L Trichloroacetic acid 1.0 µg/L 1,2-Dichlorobenzene 0.2 µg/L Haloacetonitriles 1,3-Dichlorobenzene 0.2 µg/L Bromochloroacetonitrile 0.5 µg/L 1,4-Dichlorobenzene 0.2 µg/L Dibromoacetonitrile 0.5 µg/L Dichlorodifluoromethane 0.2 µg/L Dichloroacetonitrile 0.5 µg/L 1,1-Dichloroethane 0.2 µg/L Trichloroacetonitrile 0.5 µg/L 1,2-Dichloroethane 0.2 µg/L Inorganic compounds 1,1-Dichloroethylene 0.2 µg/L Chloral hydrate 0.5 µg/L cis-1,2-Dichloroethylene 0.2 µg/L Chlorate 10 µg/L

Methods of Investigation 11

XAD-8Column

DOC4

sorbed onto or leached from column

Hydrophobicneutrals

XAD-4Column

DOC7

sorbed onto or leached from column

Hydrophilicneutrals

XAD-4 Eluate - DOC6

XAD-4 Effluent - DOC5

NaOH

Hydrophilic organic acids

Low molecular weight hydrophiliccompounds

XAD-8 Eluate - DOC3NaOH

XAD-8 Effluent - DOC2

Hydrophobic organic acids

Sample In - DOC1

Figure �. Schematic diagram of organic compounds isolated using XAD-8 and XAD-4 resin columns during the fractionation procedure. (DOC, dissolved organic carbon; NaOH, sodium hydroxide)

1� Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Quality Assurance Program

A quality-assurance program was designed to evalu-ate the accuracy and precision of the water-quality data and ensure that results are representative of actual environmental concentrations. Quality-assurance samples were collected following procedures in Koterba and others (1995). Replicate samples (20 percent of environmental samples) were col-lected in succession to determine whether sample-collection techniques were reproducible, the chemical composition of the water sample changed during sample collection, and analyti-cal results were reproducible. Equipment blanks (20 percent of environmental samples) were collected prior to sampling and after the final well was sampled during the two sampling rounds to determine whether analytical results were biased by interferences introduced during the process of cleaning and storing sample collection equipment, or during sample collec-tion, handling, preserving, or shipping procedures. Nitrogen-purged VOC-free blank water, obtained from NWQL, was used for organic blanks. Inorganic blank water, obtained from the USGS Quality Water Service Unit Laboratory in Ocala, Florida, was used for inorganic blanks. Quality-assurance procedures for reported data included checking the ion balance for each sample, comparing field and laboratory pH, specific conductance, and alkalinity values, and requesting reruns if any aspects of the results were questionable.

The internal quality-control program followed by the NWQL is documented by Friedman and Erdmann (1982) and Pritt and Raese (1995). The NWQL participates in the USGS Quality Assurance Program, under which standard samples are

submitted for analysis and tabulated statistics on the results are reported.

Results of analysis of field-replicate samples are listed in appendix 1a. Differences between concentrations of replicate samples are within the uncertainty of the significant figures used in reporting concentrations. Concentrations detected in blank samples also are listed in appendix 1a. Summary information is listed in table 7. Concentrations of DOC were detected by the NWQL and the Boulder, Colorado, labora-tories in the pre-sampling blank collected on July 21, 1998. Low-level organic-carbon contamination was present in the volatile-grade blank water (K.D. Pirkey, NWQL, writ-ten commun., 1998). Silica was present in the first blank because of contamination from the borosilicate glass nitric acid ampule (E.J. Zayhowski, NWQL, oral commun., 1998) but no explanation can be made for the low-level detection of ammonia. Results of the analysis of the blank collected August 27, 1998, yielded no detectable concentrations with the exception of DOC and TOC detections by the Boulder, Colorado, laboratory. The low-level concentrations of silica and ammonia detected in the first blank are not sufficiently great to negatively affect the environmental data. Concentra-tions of DOC and TOC were consistently less in samples analyzed by NWQL compared with those in samples analyzed in the Boulder, Colorado, laboratory. Because of analytical and instrument variability associated with low organic carbon concentration samples, the differences are within acceptable limits. The results from the Boulder laboratory are not pre-sented in this report.

Data on DBP formation in equipment blanks also are summarized in table 7 and presented in appendix 1-2. Of the

Table �. Summary of organic carbon fractions isolated using XAD-8 and XAD-4 resin columns during fractionation procedure.

[DOC, dissolved organic carbon; NaOH, sodium hydroxide; <, less than; >, greater than]

Fraction Description Organic carbon species

DOC 1 XAD-8 influent (sample before fractionation onto XAD-8 column)

All measurable organic carbon in sample

DOC 2 XAD-8 effluent - all that passes through column Hydrophilic organic acids and neutralsLow-molecular-weight hydrophilic compounds

DOC 3 XAD-8 eluate - compounds initially retained on XAD-8 column and eluted with NaOH

Hydrophobic organic acids (humic and fulvic acids)5-9 carbon aliphatic acids1 and 2 ring aromatic carboxylic acids1 and 2 ring phenols

DOC 4 DOC 1 - [DOC 2 + DOC 3] calculated value

Calculated – hydrophobic organic neutrals; > 0, retained on column, < 0, leached from column

DOC 5 XAD-4 effluent - all that passes through column Low-molecular-weight hydrophilic compounds

DOC 6 XAD-4 eluate - compounds initially retained on XAD-4 column and eluted with NaOH

Hydrophilic organic acids; polyfunctional organic acids;< 6-carbon aliphatic acids

DOC 7 DOC 2 - [DOC 5 + DOC 6] calculated value

Calculated – hydrophilic organic neutrals;> 0, retained on column, < 0, leached from column

Methods of Investigation 1�

Table �. Summary of types, purpose, and results of quality-assurance and quality-control analyses for water-quality samples from 20 community water-supply wells, New Jersey, 1998-99.

[NWQL, U.S. Geological Survey National Water Quality Laboratory; NJWSC, New Jersey Water Science Center; EHL, Environmental Health Laboratory; VOC, volatile organic compound; DOC, dissolved organic carbon; TOC, total organic carbon; mg/L, milligrams per liter; MRL, method reporting limit; DBPs, disinfection by-products; THMs, trihalomethanes; HAAs, haloacetic acids; UV-254, ultraviolet absorbance at 254 nanometers]

Type of sample: Laboratory used and number of samples

(x)

Purpose, results, and conclusions

Blanks Purpose: To determine whether analytical results may be biased by interferences introduced during equipment cleaning and storage, sampling procedures, shipping, or laboratory analysis.

Source Water: NWQL(2)

Results: Organics: No VOCs detected in blank. NWQL: DOC and TOC detected at 0.2 mg/L in one sample using VOC blank water assayed at 0.2 mg/L DOC. Inorganics: Ammonia detected at 0.022 mg/L, MRL 0.02 mg/L; silica 0.14 mg/L, MRL, 0.10 mg/L in one sample. Silica source

is borosilicate glass nitric acid ampule.Conclusions: Equipment cleaning and storage, field-sampling methods, and laboratory analytical techniques did not introduce

any significant biases in the results.Boulder, Colorado (2)

Results: Organics: Concentrations of DOC and TOC were from 0.4 to 0.5 mg/L for blanks. No absorbance was measured in UV-254

analysis. Conclusions: Organics: Boulder, Colorado: Concentrations of TOC and DOC were consistently greater than those determined by NWQL.

Detections of DOC and TOC in blanks from 1998 may explain some DBP detections in blanks chlorinated by EHL. UV-254 results were reproducible; no bias is introduced.

New Jersey Water Science Center laboratory (2)

Results: One UV-254 of 0.002, less than any environmental samples.Conclusions: UV-254 results were reproducible; no bias is introduced.

Disinfection by-products:EHL (2)

Results: Organics: THMs and HAAs were detected in blanks; some detections may result from organic carbon contamination of blank

water.Inorganics: High concentrations of chlorate and chloral hydrate were detected in several blanks; all blanks contained detectable

levels of these two constituents.Conclusions: Organics: Concentrations of organic DBPs were less than some of the environmental concentrations. If the detections result

from organic carbon contamination of the blank water, then environmental sample concentrations are presumed to be unaffected. Inorganics: The environmental data cannot be interpreted because of the high concentrations of both chlorate and chloral

hydrate in the blanks.

Replicates Purpose: To determine whether samples collected in succession are homogeneous, sample collection techniques and laboratory analytical techniques are reproducible.

Source Water:NWQL, (2)

Results: Organics and Inorganics: Replicates were within expected range of reproducibility.Conclusions: Analytical results were reproducible, no bias is introduced.

Boulder, Colorado(2)

Results: Organics: Organic-carbon replicates were within expected range of reproducibility; one UV-254 replicate had 40 percent variability.Conclusions: Organic-carbon results were reproducible; no bias is introduced. Some UV-254 measurements may be affected by high iron concentrations.

New Jersey Water Science Center laboratory (2)

Results: Replicates were within expected range of reproducibility.Conclusions: Analytical results were reproducible; no bias is introduced.

Disinfection by-products:EHL(2)

Results:Organics: High variability in concentrations of HAA in three of four replicate sets.Inorganics: Replicates were within expected range of reproducibility.Conclusions: Organics: HAA data need to be interpreted qualitatively.Inorganics: Analytical results were reproducible, but interpretation is not possible because of high concentrations in blanks.


THMs, chloroform was detected in all blanks at concentra-tions ranging from 0.7 to 6.8 µg/L; bromodichloromethane and dibromochloromethane were detected at 0.8 and 0.1 µg/L, respectively, in one blank. Eight environmental samples contained chloroform at a concentrations less than the high blank concentration. Four of the five HAAs (bromochloro-acetic acid, dichloroacetic acid, monochloroacetic acid, and trichloroacetic acid) were detected in from one to three of the four blank samples. Some of the HAA detections in the blanks were less than the environmental samples, but many were at similar levels. Low-level organic carbon contamina-tion of the blank water may be the cause of the detections of chloroform and HAAs in the blanks from 1998. No HANs were detected in the blank samples. Chlorate was detected in the blank samples at concentrations ranging from 95 to 2,100 µg/L. Chloral hydrate was detected in the blank samples at concentrations ranging from 1.2 to 120 µg/L—the concentra-tion of 120 µg/L was reported as “high biased,” being more than an order of magnitude greater than the high concentration in the environmental samples. Because of the wide range and high bias of concentrations in the blanks, interpretation of the chlorate and chloral hydrate data for environmental samples is not possible; thus, chlorate and chloral hydrate incubation data for environmental samples are not reported.

Quality of Source Water to Community Water-Supply Wells

The water samples that were collected from the 20 com-munity water-supply wells are representative of the water withdrawn from the well before treatment. The water that reaches the open interval of a large-volume well, such as a supply well, may originate, in part or entirely, from areas outside the immediate area of the wellhead, depending upon factors such as well depth, aquifer characteristics, location of the well in the local flow system, and stresses created on that flow system by other pumped wells. Because supply wells withdraw large volumes of water, water containing contami-nants originating in part of the contributing area to the well may be diluted by uncontaminated water from other parts of the contributing area as mixing of water takes place in the immediate vicinity of, or within, the well bore. Consequently, concentrations of contaminants in water from supply wells may not represent the maximum concentrations in at least some part of the source water.

Results of the water-quality analyses indicate that con-taminants are present at concentrations that exceed MCLs in water from some of the wells sampled, and pH and constitu-ents exceed New Jersey SMCLs in water from several wells. In other wells, however, several constituents that are consid-ered contaminants were present at elevated levels that did not exceed established water-quality standards.

Volatile Organic Compounds

No VOCs were detected in water from the wells in confined aquifers of the Coastal Plain (app. 2), an anticipated result, as the four wells are located more than 30 mi down-gradient from the outcrop areas of the aquifers and withdraw water that is several thousands of years old. VOCs were detected in water from all the wells in unconfined aquifers, however. Of the aromatic VOCs (those containing one or more benzene rings), the most common are components of gasoline and other petroleum compounds; these often are referred to as BTEX—for benzene, toluene, ethylbenzene, and xylenes. Ben-zene was the only BTEX compound detected; it was detected in water from wells in the unconfined aquifers. Benzene was detected at a concentration less than the MRL in water from a well (030460) completed in a bedrock aquifer and a concentra-tion of 0.5 µg/L—less than the MCL of 1 µg/L—in water from a well (291264) completed in a Coastal Plain aquifer. Other aromatic VOCs—1,2-dichlorobenzene, 1,3-dichlorobenzene, and 1,4-dichlorobenzene—were detected, but only in water from the Coastal Plain well (291264) in which benzene was detected (app. 2).

Commonly detected aliphatic compounds include chlo-rinated solvents such as tetrachloroethylene (PCE), trichloro-ethylene (TCE), and the compound currently used to oxygen-ate gasoline— methyl tert-butyl ether (MTBE). At least one aliphatic VOC was detected in water from each well in the unconfined aquifers (app. 2). The most commonly detected aliphatic VOC was MTBE, in water from 13 of the 16 wells in unconfined aquifers (fig. 4a); none of the concentrations exceeded the MCL of 70 µg/L, however. TCE, the next most commonly detected compound, was present in water from 11 of the 16 wells in the unconfined aquifers. Concentrations of TCE exceeded the MCL (1 µg/L) in water from six wells, ranging from 1.32 to 43 µg/L (fig. 4b). Other compounds with high detection frequencies in water from the wells in unconfined aquifers were 1,1,1-trichloroethane (10 wells), 1,1-dichloroethane and cis-1,2-dichloroethylene (9 wells each), and PCE (8 wells). None of the first three compounds were present at concentrations that exceeded MCLs (30, 50, 70, and 1 µg/L, respectively), but concentrations of PCE exceeded the MCL in water from five of the eight wells (fig. 4c). TCE and PCE exceeded MCLs in water from more wells in bedrock aquifers than in water from wells in either glacial or Coastal Plain aquifers. The concentration of 1,2-dichloro-ethane exceeded the MCL (2µg/L) in water from one Coastal Plain well, but not in water from the other six wells in which it was detected. Carbon tetrachloride was detected in water from three wells, exceeding the MCL (2µg/L) in water from one well (030460) in a bedrock aquifer.

The compound cis-1,2-dichloroethylene is a degradation product of PCE and TCE; its presence, therefore, indicates that biodegradation of the parent compounds is occurring in the aquifers. A further degradation product, vinyl chloride, was not detected in water from any of the sampled wells, however.

Quality of Source Water to Community Water-Supply Wells 1�

Glac

ial

Unco

nfin

ed C

oast

al

Plai

n

Bedr

ock

Conf

ined

Coa

stal

Pl

ain

EXPL

ANAT

ION

AQUI

FER

TYPE

2700

80 2701

47 2701

55 2701

82 3904

51 0500

3907

0177 07

0368 15

0207 23

0195 29

1264 01

0039 01

0600 09

0136 15

0276 03

0301 03

0460 13

0098 21

0402 35

0083

0.00

1

0.010.1110

CONCENTRATION OF CHLOROFORM, IN MICROGRAMS PER LITER

WEL

L N

UM

BER

100

dc

2700

80 2701

47 2701

55 2701

82 3904

51 0500

3907

0177 07

0368 15

0207 23

0195 29

1264 01

0039 01

0600 09

0136 15

0276 03

0301 03

0460 13

0098 21

0402 35

0083

0.00

1

0.1110100

CONCENTRATION OF PCE, IN MICROGRAMS PER LITER

WEL

L N

UM

BER

0.01

b

2700

80 2701

47 2701

55 2701

82 3904

51 0500

3907

0177 07

0368 15

0207 23

0195 29

1264 01

0039 01

0600 09

0136 15

0276 03

0301 03

0460 13

0098 21

0402 35

0083

0.00

1

0.010.1110

CONCENTRATION OF TCE, IN MICROGRAMS PER LITER

WEL

L N

UM

BER

100

aN

ew J

erse

y D

rinki

ng W

ater

Sta

ndar

d =

70 m

icro

gram

s pe

r lite

r

2700

80 2701

47 2701

55 2701

82 3904

51 0500

3907

0177 07

0368 15

0207 23

0195 29

1264 01

0039 01

0600 09

0136 15

0276 03

0301 03

0460 13

0098 21

0402 35

0083

0.00

1

0.1110100

CONCENTRATION OF MTBE, IN MICROGRAMS PER LITER

WEL

L N

UM

BER

0.01

MCL

= 1

mic

rogr

am p

er li

ter

MCL

= 1

mic

rogr

am p

er li

ter

TTH

M M

CL =

80

mic

rogr

ams

per l

iter

Figu

re �

. Co

ncen

tratio

ns o

f (a)

met

hyl t

ert-b

utyl

eth

er (M

TBE)

, (b)

tric

hlor

oeth

ylen

e (T

CE),

(c) t

etra

chlo

roet

hyle

ne (P

CE),

and

(d) c

hlor

ofor

m in

wat

er fr

om 2

0 co

mm

unity

w

ater

-sup

ply

wel

ls in

New

Jer

sey,

by

aqui

fer t

ype,

199

8-99

. (M

CL, m

axim

um c

onta

min

ant l

evel

; TTH

M, t

otal

trih

alom

etha

nes;

TTH

M M

CL is

the

sum

of b

rom

ofor

m,

brom

odic

hlor

omrth

ane,

dib

rom

ochl

orom

etha

ne, a

nd c

hlor

ofor

m c

once

ntra

tions

)


Of the THMs, chloroform was detected in water from 12 wells completed in unconfined aquifers. Most detections were at low concentrations (0.05-0.93 µg/L) in samples from nine of the wells, but this compound was present at a concentration of 2.4 µg/L in water from a well in a bedrock aquifer, at 4.10 µg/L in water from a well in a glacial aquifer, and at 37.9 µg/L in water from a well in a Coastal Plain aquifer (fig. 4d). In addition, a low concentration of bromodichloromethane (0.5 µg/L) was detected in water from one Coastal Plain well—and at estimated concentrations less than the MRL in water from two other wells. Thus, two compounds that occur as DBPs in treated drinking water also are present in the untreated water.

Nutrients

Nutrients is a term that includes compounds such as ammonia, nitrate, and phosphate. Ammonia was not detected in water from wells in the bedrock and glacial aquifers, but was detected in water from all sampled wells in the Coastal Plain aquifers (fig. 5a). Overall, water from wells in the unconfined aquifers contained higher concentrations of ammonia than did water from wells in the confined aquifers; the median concentrations were 0.54 and 0.16 mg/L, respec-tively. Concentrations of ammonia in water from the uncon-fined aquifers are a likely indication of anthropogenic inputs. The presence of ammonia in water from wells in the confined aquifers is indicative of a nitrogen source in the aquifer, as the water tapped by these wells is too old to have been affected by human activities. Naturally occurring organic materials in the sediments, which have been converted to lignite during the millions of years since deposition, are a likely source of nutrients. (The detections of orthophosphate in water from wells in the confined aquifers (app. 2) also could be indicative of organic matter in the aquifers.) Reducing conditions exist in the parts of the confined aquifers tapped by the sampled wells, as there is little if any DO present in the water; thus, the nitrogen in these aquifers is not oxidized to nitrate, but is present as ammonia. There is no New Jersey or Federal MCL for ammonia in drinking water, but its presence in drinking water is of interest because, under oxidizing conditions, it can be converted to nitrate.

Nitrite (as N) was detected in water from only one well in a glacial aquifer, at a concentration of 0.03 mg/L, which does not exceed the MCL (1 mg/L as N). Nitrate was not detected in water from any of the wells in confined aquifers, but was detected in water from five of the six wells in unconfined Coastal Plain aquifers and in water from all wells in bedrock and glacial aquifers. Concentrations of nitrate were less than the drinking water MCL of 10 mg/L as N in all samples; the highest concentrations—3.63 and 4.86 mg/L—were in water from wells in bedrock aquifers; one well in a Coastal Plain aquifer yielded water containing 3.19 mg/L (fig. 5b). Madison and Brunett (1985) indicate that concentrations of nitrate in ground water that exceed 3 mg/L represent effects of human activities, whereas Perlmutter and Koch (1972) state that

concentrations in excess of 1 mg/L are indications of nitrogen inputs by human activities. Using the latter criterion, water from all wells in the bedrock aquifers, from three of the five wells in glacial aquifers, and from two wells in the unconfined Coastal Plain aquifers has been affected by inputs of nitrogen resulting from human activities. Although concentrations of nitrate were low in three other wells in unconfined Coastal

Glacial

Unconfined Coastal Plain

Bedrock

Confined Coastal Plain

EXPLANATION

AQUIFER TYPE

0.001

0.01

0.1

1

10

CON

CEN

TRAT

ION

OF

AMM

ONIA

, IN

MIL

LIGR

AMS

PER

LITE

R

WELL NUMBER

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83

a

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

830.001

0.01

0.1

1

10

CON

CEN

TRAT

ION

OF

NIT

RITE

+ N

ITRA

TE, I

N

MIL

LIGR

AMS

PER

LITE

R

b

WELL NUMBER

Maximum contaminant level = 10 milligrams per liter

Figure �. Concentrations of (a) ammonia and (b) nitrite + nitrate in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99.

Quality of Source Water to Community Water-Supply Wells 1�

Plain aquifers, concentrations of DO also were low (0.1 mg/L) in water from those wells, and concentrations of ammonia were high (0.72-1.35 mg/L). Consequently, nitrate probably had been reduced (or ammonia never oxidized), and nitrogen inputs likely were in the range indicating human activities rather than natural conditions.

Concentrations of phosphate ranged from undetectable (at 0.01 mg/L as P) to 0.29 mg/L as P. The highest concen-trations were in water from wells completed in the confined Coastal Plain aquifers, the lowest (undetected) in water from wells in three unconfined Coastal Plain aquifers (app. 2). The materials that compose two of these latter unconfined Coastal Plain aquifers (the Kirkwood Formation and Cohansey Sand; and the Oldbridge Formation, part of the Potomac-Raritan-Magothy aquifer system) are primarily quartz sand with minor amounts of organic matter. The third, the unconfined updip part of the Lower Potomac-Raritan-Magothy aquifer system, is also primarily quartz sand. Within this lower part of the aquifer system, silt and clay layers contain sporadic occur-rences of organic materials, including woody fragments, but wells are unlikely to be completed in these layers. The other Coastal Plain formations (Magothy, sand units of the Raritan, Lower Kirkwood) that form unconfined and confined aquifers all contain carbonaceous materials (Owens and Sohl, 1969). The highest concentrations of phosphate were in water from the downdip (confined) Lower Kirkwood aquifer, which con-tains not only finely comminuted carbonaceous material, but fossils that indicate a marine origin. Thus, it is likely that the concentrations of phosphate in the Coastal Plain aquifers are mainly related to the abundance, or lack thereof, of naturally occurring organic materials.

Concentrations of phosphate in water from wells com-pleted in the bedrock aquifers were low but detectable. The soils developed on the bedrock formations are, for the most part, rich in clays to which anthropogenic phosphate from land-surface or subsurface sources would likely adsorb. Phos-phorus apparently is present in these sedimentary formations, because the mineral apatite (Ca5(PO4)3) is reported in contact-metamorphosed rocks adjacent to diabase intrusions (Van Houten, 1969). The concentrations of phosphate in water from the bedrock wells may derive, at least in part, from naturally occurring materials.

Concentrations of phosphate in water from the gla-cial-aquifer wells were in the same range (0.01-0.10 mg/L) as those in water from the bedrock wells. Both natural and anthropogenic sources are possible; assessing potential geo-logic inputs is complicated by the heterogeneous nature of geologic sources for the glacial deposits.

Major and Minor Ions, Trace Elements, and pH

Concentrations of chloride in water from wells completed in the Coastal Plain aquifers were all less than 50 mg/L; the lowest concentrations (less than 10 mg/L) were in water from three of the four wells completed in the confined Atlantic City

800-foot sand (a unit within the Kirkwood-Cohansey aquifer system). Concentrations in water from four of the five wells in glacial aquifers exceeded 50 mg/L; the concentrations of chloride in one sample was 113 mg/L. Concentrations of chlo-ride in water from three of the five wells in bedrock aquifers exceeded 50 mg/L; the concentration in water from one well (030301) was 634 mg/L (fig. 6a), more than twice the SMCL of 250 mg/L, and substantially higher than concentrations of chloride previously reported for ground water in northeastern New Jersey (Szabo and others, 1989). The concentrations of sodium in water from this well was 209 mg/L—more than 4 times the SMCL of 50 mg/L. Water from this well also contained concentrations of PCE and TCE that exceeded their respective MCLs; clearly, contaminants from human activi-ties have affected the quality of water that is being withdrawn from this well. These results indicate that anthropogenic inputs also could account for the elevated concentrations of sodium and chloride.

Concentrations of sodium in water from 15 of the 16 wells completed in unconfined aquifers, and 3 of the 4 wells in confined aquifers were less than 50 mg/L (fig. 6b). Water from the well (150276) in the confined Potomac-Raritan-Magothy aquifer system contained sodium at a concentration of 67.3 mg/L, however, with a corresponding chloride concentration of 27.9 mg/L. Additionally, the concentration of fluoride in water from this well was the highest (1.4 mg/L) measured in the water sampled during this study; this concentration did not exceed the MCL. The concentrations of fluoride in water from well 150276 undoubtedly are derived from natural sources.

Concentrations of sulfate, with one exception, were less than 60 mg/L in water from wells in all the unconfined aquifers and less than 20 mg/L in water from two Coastal Plain wells in unconfined aquifers. The water from the wells in confined Coastal Plain aquifers contained concentrations of sulfate at less than 20 mg/L. The highest concentration (623 mg/L) was measured in water from a well (350083) in a northeastern New Jersey bedrock aquifer, and exceeded the SMCL of 250 mg/L (fig. 6c; app. 2). In this aquifer (part of the Passaic Formation), concentrations of this magnitude are most likely to be natural, resulting from dissolution of sulfate min-erals such as gypsum (Szabo and others, 1989). The concen-tration of calcium in the sample from this well also was high (271 mg/L), supporting the likelihood that aquifer minerals (gypsum, in this case) substantially affect the chemistry of the ground water.

Fluoride was detected in water from only one well in the bedrock aquifers, from two wells in unconfined Coastal Plain aquifers, and in none of the wells in glacial aquifers. Water from all four of the confined Coastal Plain aquifers contained fluoride at detectable concentrations (0.2-1.4 mg/L). No con-centrations were greater than the MCL.

Bromide was detected in water from all 18 wells for which it was analyzed. For the entire set of 20 wells, concen-trations of bromide tended to increase as concentrations of chloride increased (r2 = 0.38, p = 0.006); for wells in a par-ticular aquifer type, the relation was strongest for the wells in


confined Coastal Plain aquifers (fig. 7). The concentration of bromide can affect the concentration of the bromide-contain-ing species of the THMs.

Concentrations of iron in water from the 20 wells ranged widely—from less than the MRL (10 µg/L) to nearly 7,000 µg/L. Although soils and aquifer materials may contain sub-stantial amounts of iron, it is commonly present in minerals of low solubility. Low pH and reducing conditions in the aquifer can promote dissolution of minerals and solubilization of iron, however. The highest concentrations of iron, which exceeded the SMCL (0.3 mg/L), were in acidic water from four wells in unconfined Coastal Plain aquifers where the concentrations of DO (and nitrate) were low. Concentrations of iron in water from the confined Coastal Plain aquifers were at least an order of magnitude less than those in water from the unconfined Coastal Plain aquifers. Iron was not detected (reported as <10 µg/L) in water from all wells in the bedrock aquifers, one well in unconfined Coastal Plain aquifers, and two wells in glacial aquifers; concentrations were estimated at less than 10 µg/L in water from two other glacial-aquifer wells (app. 2).

The chemical behavior of manganese shows some simi-larities to that of iron. Concentrations of manganese were low (estimated at 2-3 µg/L) or not detected in water from all wells

c

1

10

100

1000

WELL NUMBER

CON

CEN

TRAT

ION

OF

SULF

ATE,

IN

MIL

LIGR

AMS

PER

LITE

R

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83

Secondary maximum contaminant level = 250 milligrams per liter

b

1

10

100

1000

WELL NUMBER

CON

CEN

TRAT

ION

OF

SODI

UM, I

N

MIL

LIGR

AMS

PER

LITE

R

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83


Glacial


Bedrock


EXPLANATION

AQUIFER TYPE

a

1

10

100

1000

WELL NUMBER

CON

CEN

TRAT

ION

OF

CHLO

RIDE

, IN

M

ILLI

GRAM

S PE

R LI

TER

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83


Figure �. Concentrations of (a) chloride, (b) sodium, and (c) sulfate in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99.

0.25

0.20

0.15

0.10

0.05

0.00

BRO

MID

E CO

NCE

NTR

ATIO

N, I

N M

ILLI

GRA

MS

PER

LITE

R

CHLORIDE CONCENTRATION, IN MILLIGRAMS PER LITER

1 10 100 1,000

Glacial


Bedrock


EXPLANATION

R2 = 0.38p-value = 0.006

AQUIFER TYPE

Figure �. Relation of concentrations of bromide to concentrations of chloride in water from 20 community water-supply wells in New Jersey, 1998-99.

Quality of Source Water to Community Water-Supply Wells 19

in the bedrock aquifers, one well in an unconfined Coastal Plain aquifer, and four wells in glacial aquifers. Concentra-tions also were generally low (20 µg/L or less) in water from the confined aquifers, but were high (70-1,830 µg/L) in water from five wells in unconfined Coastal Plain aquifers, including the four yielding water with high concentrations of iron (app. 2). The high concentrations of manganese all exceeded the SMCL of 50 µg/L.

The pH of water from 14 of the 20 wells was generally near neutral to slightly alkaline (6.7-8.1; median 7.4), but water from wells in the unconfined Coastal Plain aquifers was strongly to slightly acidic (pH 4.7-6.5). The pH of water from five of the six wells in the unconfined Coastal Plain aquifers was outside the New Jersey optimum range for pH in drinking water (6.5-8.5; table 2).

Organic Carbon

Concentrations of DOC in the ground-water samples were about the same as those of TOC, indicating that there was little particulate organic matter present. Water from wells with high-volume output is less likely to be turbid (contain-ing particles) because there is less opportunity for particles to accumulate than in water from wells pumped only sporadi-cally. Concentrations of both TOC and DOC were less than 2 mg/L in all samples, with the highest values being measured in water from several wells in unconfined Coastal Plain and glacial aquifers (app. 2). The sample from one glacial-aquifer well (270147) contained not only high concentrations of DOC (1.40 mg/L), but several VOCs, with some concentrations exceeding MCLs.

UV-254 values were generally higher in ground water from the Coastal Plain aquifers, both confined and unconfined, than those in water from the bedrock and glacial aquifers, in some cases by an order of magnitude (fig. 8). Only for the sample from one glacial-aquifer well (270147) was the UV-254 value comparable to the UV-254 measurements for samples from the Coastal Plain wells.

Dissolved Organic Carbon Fractions and Disinfection By-Products

DOC consists of a variety of compounds that can be grouped by fractionation techniques on the basis of their chemical behavior. Interactions of DOC and its groups of com-pounds with chlorine to form DBPs can be examined through laboratory incubation studies.

Organic Carbon Fractions

Humic substances constitute the largest proportion of the compounds that compose DOC. They are found in all terres-trial and aquatic environments. Humic substances constitute

a class of yellow-black decomposition products of plant and animal organic matter; they are refractory and resistant to deg-radation (Aiken, 1985). The physical and chemical characteris-tics of humic substances are, as yet, not well defined, but they have been shown to have high molecular weights and carbon skeletons with a high degree of aromaticity. Humic substances typically are divided into operationally defined fractions on the basis of their solubility in dilute acids and bases. Fulvic acids are soluble at any pH; humic acids precipitate from aqueous solutions at a pH less than 2, and humin is insoluble at any pH. Both humic and fulvic acids are strong complexing agents; fulvic acid is a stronger reducing agent than is humic acid (Thurman, 1985). Humic substances are hydrophobic, thus they are able to transport other organic contaminants that also are hydrophobic (Wong and others, 2002). Moreover, humic substances are involved in the generation of DBPs (Rook, 1974): in fact, they are considered primary precursors of DBPs (Liang and Singer, 2003). Hydrophobic compounds are mostly removed, however, if water is treated with metal salts that coagulate much of the organic matter present (Wong and others, 2002).

Glacial


Bedrock


EXPLANATION

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83

WELL NUMBER

0.02

0.025

0.03

0.035

0.04

UV-2

54 A

BSOR

BAN

CE, A

S 1/

CEN

TIM

ETER

S0.00

0.005

0.01

0.015

AQUIFER TYPE

Figure 8. Values of ultraviolet absorbance at 254 nanometers (UV-254) in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99.

�0 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Hydrophilic acids constitute the other major component of DOC; carbohydrates, carboxylic acids, and amino acids are present in lesser amounts (Thurman, 1985). Hydrophilic acids are a complex mixture of organic acids, and are mostly anionic, although some are uncharged.

Because concentrations of DOC in the ground-water samples were low (generally about 1 mg/L or less), differ-ences in the DOC fractions in most water samples were small. Concentrations that differ by only 0.1 mg/L actually may not be different, as there is some analytical error associated with each determination. For water from the wells in Coastal Plain aquifers, concentrations of combined hydrophilic acids and neutrals, and low-molecular-weight hydrophilic compounds (the XAD-8 effluent (passes through the XAD8 column)—DOC 2) generally were as high as, or slightly higher than, those of the hydrophobic acids (the XAD-8 eluate (retained on the XAD-8 resin)—DOC 3). In samples from two wells (150207, 150276), however, concentrations of hydrophobic acids were slightly higher than concentrations of the combined hydrophilic/neutral/low-molecular weight fractions. In those samples where the hydrophilic acid fraction (passes through the XAD-8 and is retained on XAD-4 resin—DOC 6) was determined, however, concentrations of hydrophilic acids were less than those of hydrophobic acids (table 8).

Concentrations of combined hydrophilic acids and neu-trals and low-molecular-weight hydrophilic compounds (DOC 2) also were higher than those of hydrophobic acids (DOC 3) in water from wells in bedrock and glacial aquifers, with one exception (well 390451; table 8). In all water samples, the hydrophobic neutral fraction (DOC 4) was negligible. Fractions DOC 5-7 were not determined for samples from the bedrock and glacial wells.

Disinfection By-Products

SourcesFormation of DBPs was attributed to the use of chlorine

in drinking water for the first time in 1974 (Rook, 1974). The DBPs are formed when organic matter in the water reacts with the chlorine (NaOCl) used to disinfect the water used for public supply against disease-causing water-borne organisms, such as E. coli, Cryptosporidium, and Giardia. When first studied, natural organic matter was found to be an important component of the organic material that reacted with chlorine to form DBPs (Stevens and others, 1976). The major chemical species formed by the chlorination are THMs, HAAs, HANs, and chloral hydrate. Inorganic by-products, such as chlorates, also were found to form (Andrews and Ferguson, 1996).

DBPs are formed in a series of steps involving oxida-tion of organic compounds and incorporation of chlorine (and other halogens such as bromine) into the organic matter. The rates of these reactions vary. Studies indicate that some of the more likely organic compounds involved in the reactions that produce DBPs (in particular, THMs) are diketones and phe-

nols (Larson and Weber, 1994). The rate of THM formation is affected by chlorine concentration, bromide concentration, pH, and temperature (Adin and others, 1991).

Formation of Disinfection By-Products During the Laboratory Incubation Study

The concentration of THMs formed as a result of the disinfection of water supplies is known as the trihalomethane formation potential (THMFP) and is defined as the difference in concentration measured after treatment and the concentra-tion (if any) measured in the source water, as in the following equation:

THMFP = THM treated water – THM source water (1)

The concentrations of the THMs measured after a 7-day incubation of the treated water samples (table 9) varied by about two orders of magnitude, depending in part on the initial concentration of one or more THMs in the source water, but mostly on the chemical characteristics of the ground water, which are derived, in part, from characteristics and materials inherent to the aquifer from which the water was drawn.

Although chloroform was detected in source water from 12 of the 20 wells sampled, most concentrations were less than 1 µg/L. Chloroform was not detected in source water from the wells in confined aquifers or in four of the six Coastal Plain wells in unconfined aquifers. Bromodichloromethane was the only other THM detected in source water; it was present at 0.5 µg/L in the sample containing the highest concentration of chloroform (app. 2). Consequently, in most cases, the THMFP reflects all or nearly all of the THMs measured following incubation of the chlorinated water samples. In general, higher concentrations of THMs tend to form in water from the Coastal Plain aquifers than from the other aquifers from which samples were collected. Water from two wells in unconfined Coastal Plain aquifers contained total THMs at concentrations that exceed the Disinfection By-Product Rule MCL of 80 µg/L (table 1).

Using data for all wells, the concentrations of THMs, expressed as THMFP, tended to increase as UV-254 increased (r2 = 0.59) (fig. 9). The trend is controlled mainly by data for wells in glacial and unconfined Coastal Plain aquifers; data for the confined Coastal Plain and bedrock wells showed little or no trend. Regarding data for wells in unconfined Coastal Plain aquifers, concentrations of the individual THMs also tended to increase as specific UV-254 absorbance (UV-254 normalized to the concentration of DOC, or SUVA) increased (fig. 10a, b, c, d); data for wells in other aquifer types showed no trend, or positive or negative trends controlled by outliers. The relation between SUVA and chloroform (fig. 10c) was clearer; data for wells in both unconfined and confined Coastal Plain aquifers showed positive, but different trends.

In 1998, USEPA promulgated a criterion of 2.0 L/mg-m (liter per milligram-meter) for SUVA, which is calculated

Dissolved Organic Carbon Fractions and Disinfection By-Products �1

SUVA (L/mg-m) = [UV-254 (1/cm)/DOC (mg/L)] (2) x 100 (cm/m),

for a supply system’s source water prior to, and after treat-ment (U.S. Environmental Protection Agency, 1998). SUVA calculated for source water from 8 of the 20 wells equaled or exceeded the criterion (table 10). All but one of the eight wells is completed in a Coastal Plain aquifer.

The magnitude of UV-254 is related, not only to con-centration of DOC, but to the degree of aromaticity of the compounds that make up DOC. Measurements of UV-254 generally were larger in water from wells in the Coastal Plain aquifers than from wells in the bedrock aquifers and most of the wells in glacial aquifers. On the basis of the calculated SUVA value, (table 10) the DOC of Coastal Plain ground waters contains more aromatic compounds, in general, than does the DOC in water from the glacial or bedrock aquifers from which water samples were collected. Only one bedrock well (030301) yielded water of substantial aromaticity (but

low concentrations of DOC—hence high SUVA). Water from one well (270147) completed in a glacial aquifer developed high concentrations of THMs, comparable to those in water from the Coastal Plain aquifers. The UV-254 measurement for the sample from that well was high (as was the concentration of DOC); thus, the SUVA value for that sample was compa-rable to SUVA values calculated for samples from the Coastal Plain aquifers. It appears that, with both higher THMFP and higher SUVA values (tables 9 and 10), waters from the Coastal Plain aquifers generally contain more aromatic DOC and gen-erally are more prone to THM formation than water from most of the other aquifers from which samples were drawn. This indicates that, at a first approximation, measurements of UV-254 could be useful in predicting the potential of New Jersey ground water for developing THMs.

Of the THMs formed after chlorination, bromodichloro-methane (CHBrCl2), chloroform (CHCl3), and dibromochlo-romethane (CHBr2Cl) generally were present at comparable concentrations (table 9). Concentrations of bromoform

Table 8. Concentrations of dissolved organic carbon fractions in water samples from 20 community water-supply wells, New Jersey, 1998-99.

[DOC, dissolved organic carbon; mg/L, milligrams per liter; BR, bedrock; GL, glacial; CP, unconfined coastal Plain; CCP, confined Coastal Plain; nf, no fraction determined]

USGS well

number

Aquifer type

Influent, all fractions:

DOC 11 (mg/L)

Hydro-philic acids, neutrals, low

molecular weight compounds: DOC �1

(mg/L)

Hydro-phobic acids:DOC �1

(mg/L)

Hydro-phobic

neutrals: DOC �1

(mg/L)

Low molecular weight com-

pounds:DOC �1

(mg/L)

Hydro-philic acids:DOC �1

(mg/L)

Hydro-philic

neutrals:DOC �1

(mg/L)

030301 BR 1.0 0.6 0.4 0 nf nf nf030460 BR 1.0 0.6 0.3 0.1 nf nf nf130098 BR 1.0 0.6 0.4 0 nf nf nf210402 BR 0.7 0.5 0.4 2-0.2 nf nf nf350083 BR 0.7 0.6 0.3 2-0.2 nf nf nf

270080 GL 1.0 0.7 0.4 2-0.1 nf nf nf270147 GL 1.5 0.8 0.7 0 nf nf nf270155 GL 0.8 0.6 0.3 2-0.1 nf nf nf270182 GL 0.7 0.7 0.2 2-0.2 nf nf nf390451 GL 1.0 0.3 0.4 0.3 nf nf nf

050039 CP 0.8 0.7 0.3 2-0.2 0.5 0.1 0.2070177 CP 1.2 0.6 0.4 0.2 nf nf nf070368 CP 1.1 0.7 0.6 2-0.1 0.2 0.2 0.3150207 CP 1.6 0.7 0.8 2 0.1 0.5 0.3 2-0.2230195 CP 1.5 0.8 0.7 0 0.4 0.2 0.2291264 CP 1.1 0.9 0.5 2-0.3 nf nf nf

010039 CCP 0.9 0.5 0.3 0.1 nf nf nf010600 CCP 0.6 0.4 0.3 2-0.1 nf nf nf090136 CCP 0.8 0.3 0.3 0.2 nf nf nf150276 CCP 0.9 0.4 0.5 0 nf nf nf

1 See table 6 and figure 3 for full description of each DOC fraction.2 Mathematical artifact of the bias and precision of DOC fractionation and analysis scheme mass balance.

�� Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

(CHBr3) were consistently lower than those of the other THMs formed; water from several bedrock aquifers developed higher concentrations than did water from most of the other aqui-fer types. Overall, concentrations of CHBr2Cl and CHBrCl2 generally increased as concentrations of DOC increased (fig. 11a, b), with the trend largely controlled by relations between DOC and concentrations of the brominated compounds in water from glacial and the Coastal Plain aquifers. Relations between CHBr3 and DOC were unclear; only data for the unconfined Coastal Plain wells showed a discernible positive linear trend (not illustrated). Regarding the data for all wells, virtually no relation was observed for the CHCl3 formed after treatment and concentration of DOC (fig. 11c); CHCl3 in water from confined Coastal Plain aquifers showed a negative trend with concentration of DOC. Concentrations of CHCl3 in the incubated samples are considered with caution, however, as this compound was detected in all four blanks chlorinated in 1998 and 1999. It is likely that concentrations of CHCl3 in the

Table 9. Concentrations of trihalomethanes in laboratory chlorinated ground-water samples from 20 community water-supply wells, New Jersey, 1998-99, following a 7-day incubation period.

[Total THMs, sum of bromodichloromethane, bromoform, chloroform, and dibromochloromethane; THMFP, trihalomethane formation potential (Total THMs – Total environmental THMs); BR, bedrock; GL glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; THMs, trihalomethanes; µg/L, micrograms per liter; mg/L, milligrams per liter; nd, no data; Number in parentheses is parameter code used to identify the constituent, property, or character-istic in the U.S. Geological Survey National Water Information System (NWIS) database.]

USGS well

number

Aquifer type

Bromodi-chloro

methane(CHBrCl�)

(µg/L)(99�0�)

Bromoform (CHBr�)

(µg/L)(99�0�)

Chloroform(CHCl�)(µg/L)

(99�0�)

Dibromo-chloro-

methane(CHBr�Cl)

(µg/L)(99�0�)

TotalTHMs(µg/L)

THMFP (µg/L)

Bromide(mg/L)(�18�0)

030301 BR 7.7 5.7 4.8 8.5 27 27 0.19030460 BR 5.7 2.5 6.5 4.9 20 17 0.058130098 BR 4.4 3.1 2.6 5.6 16 15 0.18210402 BR 6.7 3.7 4.9 6.3 22 22 0.083350083 BR 3.2 0.6 3.1 2.5 9.4 9.1 0.098

270080 GL 7.2 1.4 8.2 4.7 21 21 0.048270147 GL 15 1.1 29 7.9 53 53 0.043270155 GL 5.8 2.5 7.5 5.4 21 17 0.053270182 GL 2.8 1.1 2.2 2.8 8.9 8.9 0.062390451 GL 9.4 1.8 6.5 8.2 26 25 0.086

050039 CP 9.1 0.4 54 3.8 67 29 0.045070177 CP 15 1.0 17 7.1 40 40 0.12070368 CP 3.7 1.0 6.2 2.2 13 13 0.051150207 CP 40 5.9 32 30 110 110 0.15230195 CP 29 2.2 35 17 83 83 nd291264 CP 17 0.4 34 5.8 57 56 nd

010039 CCP 8.6 0.2 31 3.2 43 43 0.021010600 CCP 8.8 <0.1 30 2.3 41 41 0.026090136 CCP 14 1.9 22 10 48 48 0.036150276 CCP 17 1.7 18 12 49 49 0.11

chlorinated samples from the community water-supply wells are actually slightly lower than reported.

The chlorine added to disinfect water oxidizes bromide to hypobromous acid, which reacts with components of DOC to produce the bromine-containing DBPs (Liang and Singer, 2003). The concentrations of CHBr3 formed in the treated water samples from 18 of the community water-supply wells increased as the concentrations of bromide in the untreated (source) water increased (bromide was not measured in samples from two wells); the individual trends for samples from the different aquifer types were all generally positive (fig. 12a). Relations with source-water bromide were less strong for the other two bromine-containing THMs, CHBr2Cl (fig. 12b) and CHBrCl2 (not shown). The masses of bromide in the source-water samples are sufficient to produce the amounts of bromine-containing THMs measured in the chlorinated and incubated samples.

Concentrations of HAAs were, in general, lower by factors of 2 to 3 than those of the THMs. As with the THMs,

Dissolved Organic Carbon Fractions and Disinfection By-Products ��

however, concentrations of HAAs were higher in water from wells in the Coastal Plain than in water from wells in bedrock or glacial aquifers, with few exceptions (table 11). Concentra-tions of HAAs in water from well 210402 in a bedrock aquifer were comparable to those in water from the Coastal Plain wells, as were those in water from well 270147 in a glacial aquifer. Water from this latter well also developed high con-centrations of THMs (and contained VOCs at concentrations exceeding MCLs). Of the various HAAs, concentrations of the more highly chlorinated acids were highest; there were few detections of monochloroacetic acid. Because of detections of HAAs in field blanks that were chlorinated and incubated in the laboratory at EHL, concentrations of these compounds in the treated samples from the community water-supply wells are viewed with caution.

Concentrations of the bromine-containing HAAs were comparable to those of the highly chlorinated HAAs in water from most of the wells in bedrock and glacial aquifers, but tended to be lower than those of the highly chlorinated HAAs in water from the Coastal Plain wells. For all wells, relations between concentrations of bromine-containing HAAs such as

bromochloroacetic acid and bromide (r2 = 0.01) were weak, unlike relations between concentrations of CHBr3 and bromide (r2 = 0.49). Relations between bromide and bromochloroacetic acid for samples from wells in the different aquifer types were generally unclear or dominated by outliers.

Concentrations of HANs were undetected in water from several wells. Concentrations of individual HANs were generally less than 4 µg/L. Concentrations of dibromoaceto-nitrile generally were similar to or slightly higher than those of bromochloroacetonitrile and substantially higher than the most highly chlorinated HAN (dichloroacetonitrile), which was detected in water from only four wells (table 12). It would appear that the formation of HANs is driven more by the availability of bromide than that of chlorine. Overall, concen-trations of HANs were substantially lower than those of THMs and HAAs; higher concentrations of HANs tended to develop in water from Coastal Plain wells.

Formation of Disinfection By-Products in Dissolved-Organic-Carbon Fractions

Solutions of DOC fractions in water from some or all of the 20 wells were chlorinated and incubated for seven days: fractions DOC 2 (hydrophilic organic acids and neutrals, and low-molecular-weight hydrophilic compounds), DOC 3 (hydrophobic organic acids), and DOC 6 (hydrophilic organic acids) were determined. Fraction DOC 6 was not isolated in water from the bedrock and glacial wells or six of the Coastal Plain wells; therefore, only the DOC 3 fractions from these wells were chlorinated and incubated. DOC 2 fractions for several Coastal Plain wells also were not chlorinated and incu-bated (table 13). In treated DOC fractions from those selected wells in the Coastal Plain aquifers, concentrations of THMs and HAAs were higher in the DOC 3 fraction, which contains the hydrophobic humic substances, than in the DOC 6 frac-tion, which contains the hydrophilic humic acids (table 13). (Liang and Singer (2003) obtained similar results for selected surface-water drinking supplies.) Concentrations of HANs were negligible in all fractions in which they were determined. In samples from the bedrock and glacial wells, however, concentrations of total THMs in the DOC 3 and DOC 2 frac-tions were generally comparable, within a few micrograms per liter. Concentrations of total HAAs were slightly higher in the DOC 3 fraction than in the DOC 2 fraction in samples from bedrock wells and substantially higher (by factors of 1.5 to 4) in samples from confined Coastal Plain aquifers. Concentrations of total HANs generally were higher in the DOC 2 fraction than the DOC 3 fraction except for sam-ples from glacial aquifers. Overall, concentrations of total THMs were substantially higher in the DOC 3 fraction (the hydrophobic acids) from Coastal Plain water samples (median = 31.6 µg/L) than in the same fraction from bedrock and glacial water samples (respective medians = 16.3 and 15.7 µg/L). The total THM concentration in the DOC 3 fraction of the sample from glacial well 270147 was large (35.2 µg/L),

120

100

80

60

40

0

THM

FP, I

N M

ICRO

GRA

MS

PER

LITE

R

UV-254 ABSORBANCE, IN 1/CENTIMETERS

0 0.01 0.02 0.04

Glacial


Bedrock


EXPLANATION

20

0.03

R2 = 0.59p-value = 0.000

AQUIFER TYPE

Figure 9. Relation of trihalomethane formation potential (THMFP) to ultraviolet absorbance at 254 (UV-254) nanometers in water from 20 community water-supply wells in New Jersey, 1998-99.


EXPL

ANAT

ION

Glac

ial

Unco

nfin

ed C

oast

al

Plai

n

Conf

ined

Coa

stal

Pl

ain

Bedr

ock

AQUI

FER

TYPE

d35 30 25 20 15 10 0

02

46

8

SUVA

, IN

LIT

ERS

PER

MIL

LIG

RAM

-MET

ER

CHBr2Cl CONCENTRATION, IN MICROGRAMS PER LITERS

5

0102030405060

CHCl3 CONCENTRATION, IN MICROGRAMS PER LITERS

02

46

8

c

SUVA

, IN

LIT

ERS

PER

MIL

LIG

RAM

-MET

ER

b45 40 35 30 25 20 15 0

02

46

8

SUVA

, IN

LIT

ERS

PER

MIL

LIG

RAM

-MET

ER

CHBrCl2 CONCENTRATION, IN MICROGRAMS PER LITERS

10 5

a7 6 5 4 3 2 1 0

02

46

8

SUVA

, IN

LIT

ERS

PER

MIL

LIG

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ER

CHBr3 CONCENTRATION, IN MICROGRAMS PER LITERS

Figu

re 1

0.

Rela

tion

of c

once

ntra

tions

of (

a) b

rom

ofor

m (C

HBr 3),

(b) b

rom

odic

hlor

omet

hane

(CHB

rCl 2),

(c) c

hlor

ofor

m (C

HCl 3),

and

(d) d

ibro

moc

hlor

omet

hane

(CHB

r 2Cl) t

o sp

ecifi

c ul

travi

olet

abs

orba

nce

(SUV

A) in

wat

er fr

om 2

0 co

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unity

wat

er-s

uppl

y w

ells

in N

ew J

erse

y, 1

998-

99.


however. Chemical characteristics of water from this glacial well generally were similar to those of waters from the Coastal Plain wells, and thus the response to chlorination and incuba-tion apparently was similar. The presence of VOCs (primarily TCE) at elevated levels in water from this well also could have affected the propensity to develop DBPs.

Laboratory Determined Formation Rates of Disinfection By-Products in Treated Water from Community Water-Supply Wells

Because the residence time of treated water in distribu-tion systems is variable, rates of formation of disinfection by-products in treated-water samples were assessed. Water samples from seven wells (two each completed in bedrock, glacial, and unconfined Coastal Plain aquifers, and one in a confined Coastal Plain aquifer) were chlorinated and incu-bated for 6 hours, 24 hours, and 168 hours (7 days) at 25 °C at the EHL laboratory. The concentrations of THMs that developed over time in water from the Coastal Plain wells were substantially higher than those in water from the wells in glacial aquifers, which were higher than those in water from the bedrock aquifers (fig. 13a, b, c; app. 3). As concentrations increased over the 168 hours, the rate of THM formation was more rapid over the period from 6 to 24 hours (with concen-trations nearly doubling in most cases) than it was from 24 hours to 168 hours. Such a decrease in formation rate would be expected, as the concentrations of reactants (DOC, Br, and NaOCl) decrease over time. These results are consistent with

the experimental results for the incubation studies of surface water by Liang and Singer (2003).

HAA formation in the same samples generally followed a similar pattern, but the concentrations were, overall, much lower. There were fewer detections of the brominated HAAs (bromochloroacetic acid (BrClAA) and dibromoacetic acid (Br2AA)) in water from glacial and bedrock aquifers than in water from unconfined Coastal Plain aquifers (appendix 3). Br2AA never developed in water from two wells, one in a glacial aquifer and one in a confined Coastal Plain aquifer. BrClAA never developed in water from the same well in the glacial aquifer. Monochloroacetic acid (ClAA) seldom formed at detectable levels in any of the samples. Concentrations of dichloroacetic acid (Cl2AA) and trichloroacetic acid (Cl3AA) not only were substantially higher in samples from wells in the Coastal Plain aquifers than in samples from wells in bedrock or glacial aquifers, these compounds appeared to develop more rapidly, particularly in samples from wells 230195 and 010600 (app. 3). Concentrations of several HAAs remained below the MDL (<0.1 µg/L) after 6 hours of incubation in samples from three wells (390451, 350083, and 270155) in bedrock and glacial aquifers. Where detected, HAAs in sam-ples from these and the other wells in these aquifers changed little between 6 and 24 hours of incubation. Concentrations of THMs in samples from all the wells increased throughout the incubation period, however, typically doubling by 24 hours in samples from the wells in Coastal Plain aquifers. The rate of HAA formation (more HAAs formed during the first 24 hours of incubation than subsequently) appeared to be rapid in some samples (fig. 14a), whereas more THMs developed between 24 and 168 hours in some samples (fig. 13b). As reported by

Table 10. Measurements of ultraviolet absorbance at 254 nanometers (UV-254) and calculations of specific ultraviolet absorbance (SUVA) for water from 20 community water-supply wells, New Jersey, 1998-99.

[SUVA, [UV-254 / dissolved organic carbon] x 100; BR, bedrock; GL, glacial; Cp, unconfined Coastal Plain; CCP, confined Coastal Plain; cm, centimeters; L, liters; mg, milligrams; m, meters; --, cannot calculate; <, less than. Number in parentheses is parameter code used to identify the constituent, property, or characteristic in the U.S. Geological Survey National Water Information System (NWIS) database. ]

USGS well number

Aquifer typeUV-��1

(1/cm)(�0��)

SUVA�

(L/mg-m)USGS well

numberAquifer type

UV-��

(1/cm)(�0��)

SUVA�

(L/mg-m)

030301 BR 0.0074 3.5 050039 CP 0.007 1.4030460 BR 0.0074 0.78 070177 CP 0.010 1.4130098 BR 0.0072 0.78 070368 CP 0.018 1.6210402 BR 0.0064 0.60 150207 CP 0.028 2.0350083 BR <0.035 -- 230195 CP 0.035 3.5

270080 GL 0.0075 1.0 291264 CP 0.016 2.0270147 GL 0.022 1.6 010039 CCP 0.024 6.0270155 GL 0.0069 1.2 010600 CCP 0.027 6.7270182 GL <0.004 -- 090136 CCP 0.028 5.6390451 GL 0.0091 1.1 150276 CCP 0.020 2.9

1 Measured at National Water Quality Laboratory, Arvada, Colo.2 SUVA (L/mg-m) = [UV-254 (1/cm)/DOC (mg/L)] x 100 (cm/m).3 Measured at New Jersey Water Science Center laboratory, West Trenton, N.J.


Liang and Singer (2003), other researchers have found that HAAs form more rapidly than do THMs; the results in this study indicate that rates of formation of the THMs and HAAs were variable.

Of the HANs, trichloroacetonitrile (Cl3AN) was detected in no samples, regardless of incubation time. Dichloroace-tonitrile (Cl2AN) formed during the three incubation times in sample sets from the two wells (230195 and 150207) in unconfined Coastal Plain aquifers, and was detected in one of three samples in the sets from a well in a bedrock aquifer (210402) and the well in a confined Coastal Plain aquifer (010600) (app. 3). The brominated HANs, bromochloroaceto-nitrile (BrClAN) and dibromoacetonitrile (Br2AN), formed in

c35

30

25

40

20

15

10

5

00.5 1 1.5

CH

Cl 3 C

ON

CEN

TRA

TIO

N, I

N

MIC

RO

GR

AM

S P

ER L

ITER

DOC CONCENTRATION, IN MILLIGRAMS PER LITER

0

Glacial


Bedrock


EXPLANATION

b30

25

35

20

15

10

5

00.5 1 1.5

CH

Br 2C

l CO

NC

ENTR

ATI

ON

, IN

M

ICR

OG

RA

MS

PER

LIT

ER


0

a40

35

30

45

25

20

15

10

5

00 0.5 1 1.5

CH

BrC

l 2 CO

NC

ENTR

ATI

ON

, IN

M

ICR

OG

RA

MS

PER

LIT

ER


AQUIFER TYPE

Figure 11. Relation of concentrations of (a) bromodichloromethane (CHBrCl2), (b) dibromochloromethane (CHBr2Cl), and (c) chloroform (CHCl3) in chlorinated water to concentrations of dissolved organic carbon (DOC) in source water from 20 community water-supply wells in New Jersey, 1998-99.

30.0

25.0

20.0

35.0

15.0

10.0

5.0

0.00.00 0.05 0.10 0.15

CH

Br 2C

l CO

NC

ENTR

ATI

ON

, IN

M

ICR

OG

RA

MS

PER

LIT

ER

BROMIDE CONCENTRATION, IN MILLIGRAMS PER LITER

0.20 0.25

b

6.0

5.0

4.0

7.0

3.0

2.0

1.0

0.00.00 0.05 0.10 0.15

CH

Br 3 C

ON

CEN

TRA

TIO

N, I

N M

ICR

OG

RA

MS

PER

LIT

ER

BROMIDE CONCENTRATION, IN MILLIGRAMS PER LITER

0.20 0.25

a

R2 = 0.21p-value = 0.056

R2 = 0.49p-value = 0.002

AQUIFER TYPE

Glacial


Bedrock


EXPLANATION

Figure 1�. Relation of concentrations of (a) bromoform (CHBr3) and (b) dibromochloromethane (CHBr2Cl) in chlorinated water to concentrations of bromide in source water from 20 community water-supply wells in New Jersey, 1998-99.


c

0.1110100

CHBr

2Cl

WEL

L 35

0083

- BE

DROC

K

CONCENTRATION, IN MICROGRAMS PER LITER

CHBr

Cl2

CHBr

3CH

Cl3

b

0.1110100

CHBr

2Cl

WEL

L 39

0451

- GL

ACIA

L

CONCENTRATION, IN MILLIGRAMS PER LITER

CHBr

Cl2

CHBr

3CH

Cl3

6 ho

urs

24 h

ours

168

hour

s

EXPL

ANAT

ION

INCU

BATI

ON T

IME

a

0.1110100

CHBr

2Cl

WEL

L 23

0195

- UN

CON

FIN

ED C

OAST

AL P

LAIN

CONCENTRATION, IN MICROGRAMS PER LITER

CHBr

Cl2

CHBr

3CH

Cl3

Figu

re 1

�.

Trih

alom

etha

ne fo

rmat

ion

over

tim

e in

wat

er fr

om (a

) wel

l 230

195,

com

plet

ed in

a C

oast

al P

lain

aqu

ifer,

(b) w

ell 3

9045

1, c

ompl

eted

in a

gla

cial

aqu

ifer,

and

(c) w

ell

3500

83, c

ompl

eted

in a

bed

rock

aqu

ifer i

n N

ew J

erse

y, 1

998-

99. (

CHBr

3, bro

mof

orm

; CHB

r 2Cl, d

ibro

moc

hlor

omet

hane

; CHB

rCl 2, b

rom

odic

hlor

omet

hane

; CHC

l 3, chl

orof

orm

).


the sample sets from most of the wells, with the highest con-centrations developed in water from the unconfined Coastal Plain aquifers. The formation rate generally was greatest dur-ing the first 6 hours of incubation, with relatively little change in concentration occurring during the period from 24 to 168 hours of incubation.

Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types

The differences observed in DBP formation potentials can result from various causes. Relations among the observed DBP formation potentials can be affected by bias in the data and the origins of factors, primarily concentrations of constitu-ents, that could affect how DBPs form.

Possible Bias in Disinfection By-Product Data

The actual concentrations of the various DBPs in chlori-nated and incubated water samples from the 20 wells could be biased high because THMs and HAAs were detected in treated field blanks. The presence of trace amounts of organic carbon in the blank water used in 1998 could, however, have caused the THMs and HAAs to form in the blanks. This would indi-cate that the concentrations of the DBPs measured in treated water from wells in the Coastal Plain aquifers (sampled during 1998) are not biased high because the contaminated blank water was not part of the processing of samples. Thus the dif-ference in concentrations of DBPs in water samples from the Coastal Plain aquifers and those from the bedrock and glacial aquifers may be at least as large as that shown by the data. Furthermore, the concentrations of DBPs in the treated blanks are lower than those that formed in many of the environmental samples, primarily those from Coastal Plain aquifers. Should there be a systematic and uniform bias in the data caused by laboratory contamination, as opposed to contaminated blank

Table 11. Concentrations of haloacetic acids in chlorinated ground-water samples from 20 community water-supply wells, New Jersey, 1998-99, following a 7-day incubation period.

[Total HAAs, sum of bromochloroacetic acid, dibromoacetic acid, dichloroacetic acid, monochloroacetic acid, and trichloroacetic acid; µg/L, microgram per liter; BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; HAAs, haloacetic acids; <, less than. Number in parentheses is parameter code used to identify the constituent, property, or characteristic in the U.S. Geological Survey National Water Information System (NWIS) database.]

USGS well number

Aquifer type

Bromo-chloro-

acetic acid(BrClAA)

(µg/L)(99��)

Dibromo-acetic acid

(Br�AA)(µg/L)

(99�1�)

Dichloro-acetic acid

(Cl�AA)(µg/L)

(99�09)

Mono-chloro-

acetic acid(ClAA)(µg/L)

(99�08)

Trichloro-acetic acid

(Cl�AA)(µg/L)

(99�10)

Total HAAs(µg/L)

030301 BR 2.1 1.9 2.5 <0.1 1.9 8.4030460 BR 1.5 1.4 1.6 <0.1 1.4 5.9130098 BR 1.2 1.5 <0.1 <0.1 1.3 4.0210402 BR 3.2 3.7 3.2 3.8 1.7 16350083 BR <0.1 <0.1 2.0 <0.1 2.6 4.6

270080 GL 1.9 1.4 4.3 <0.1 2.3 9.9270147 GL 5.3 2.2 12 2.3 9.6 31270155 GL 2.3 2.5 2.1 2.8 1.7 11.4270182 GL 1.2 <0.1 1.5 <0.1 1.7 4.4390451 GL 2.3 1.5 2.4 <0.1 1.8 8.0

050039 CP 2.5 11 5.5 <0.1 2.7 22070177 CP 3.1 1.4 6.9 <0.1 4.0 15070368 CP 2.2 1.2 8.3 <0.1 4.8 17150207 CP 9.3 6.1 9.6 <0.1 6.9 32230195 CP 8.5 4.1 15 2.3 13 43291264 CP 3.1 1.0 10 <0.1 7.0 21

010039 CCP 3.4 <0.1 14 <0.1 18 35010600 CCP 2.5 <0.1 9.8 <0.1 4.0 16090136 CCP 4.0 2.5 6.7 <0.1 3.2 16150276 CCP 5.1 2.4 9.5 <0.1 6.9 24

Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types �9

water, the relations between concentration and groups of wells (by aquifer type) could still be valid.

Relations Among Disinfection By-Product Formation Potentials

With few exceptions, the THMFP for water from the Coastal Plain aquifers was greater (by factors of 1.5 to 4) than that for water in bedrock and glacial aquifers (fig. 15). A true haloacetic acid formation potential (HAAFP) could not be calculated, however, because HAAs were not measured in the source water. As chloroform is the only THM that is found routinely in source water, and typically at low concentrations, HAAs probably can be assumed to be absent until the water

is treated. The total concentrations of HAAs, which probably represent the HAAFP (fig. 16), were distributed among the aquifer types in a pattern similar to that of the THMFP, and there was a strong positive linear relation (r2 = 0.65) between THMFP and concentrations of total HAAs (fig. 17). Relations between total HANs and THMs (r2 = 0.39), and total HANs and total HAAs (r2 = 0.11) were substantially weaker.

Table 1�. Concentrations of haloacetonitriles in chlorinated ground-water samples from 20 community water-supply wells, New Jersey, 1998-99, following a 7-day incubation period.

[Total HANs, sum of bromochloroacetonitrile, dibromoacetonitrile, and dichloroacetonitrile; BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; µg/L, microgram per liter; HANs, haloacetonitriles. Number in parentheses is parameter code used to identify the constituent, property, or characteristic in the U.S. Geological Survey National Water Information System (NWIS) database.]

USGS well

number

Aquifer type

Bromo-chloro-

acetoni-trile

(BrClAN)(µg/L)

(99�1�)

Dibromo-acetoni-

trile(Br�AN)(µg/L)

(99�1�)

Dichloro-acetoni-

trile(Cl�AN)(µg/L)

(99�1�)

Total HANs(µg/L)

030301 BR 0.7 1.3 <0.1 2.0030460 BR 0.7 1.2 <0.1 1.9130098 BR 0.6 1.1 <0.1 1.7210402 BR 0.6 1.0 <0.1 1.6350083 BR 0.6 <0.1 <0.1 0.6

270080 GL <0.1 0.6 <0.1 0.6270147 GL 0.9 0.7 0.5 2.1270155 GL 0.6 0.9 <0.1 1.5270182 GL <0.1 <0.1 <0.1 <0.1390451 GL 1.5 1.5 <0.1 3.0

050039 CP 0.5 1.0 <0.1 1.5070177 CP <0.1 1.1 <0.1 1.1070368 CP 0.9 0.8 0.8 2.5150207 CP 3.7 5.0 1.2 9.9230195 CP 3.0 3.1 2.0 8.1291264 CP <0.1 1.1 <0.1 1.1

010039 CCP <0.1 <0.1 <0.1 <0.1010600 CCP <0.1 <0.1 <0.1 <0.1090136 CCP 12 <0.1 <0.1 12150276 CCP 0.7 1.6 <0.1 2.3

1

10

100

BrCIAA

CON

CEN

TRAT

ION

, IN

MIC

ROGR

AMS

PER

LITE

R

CIAABr2AA CI2AA CI3AA

WELL 230195 - UNCONFINED COASTAL PLAIN

b

a

1

10

100

BrCIAA

WELL 390451 - GLACIAL

CON

CEN

TRAT

ION

, IN

MIC

ROGR

AMS

PER

LITE

R

CIAABr2AA CI2AA CI3AA

6 hours

24 hours

168 hours

INCUBATION TIME

EXPLANATION

Figure 1�. Haloacetic acid formation over time in water from (a) well 390451, completed in a glacial aquifer, and (b) well 230195, completed in a Coastal Plain aquifer in New Jersey, 1998-99. (Br2AA, dibromoacetic acid; BrClAA, bromochloroacetic acid; ClAA, cloroacetic acid; Cl2AA, dichloroacetic acid; Cl3AA, trichloroacetic acid)


Origins of Selected Chemical Characteristics and Constituents and Their Effects on Disinfection By-Product Formation Potential

Several factors potentially can affect DBP formation potentials. These include concentrations and characteristics of DOC, and concentrations of bromide. Concentrations of iron, manganese, and ammonia, which may be indicative of redox conditions, presence of colloids, or complexation with organic matter, also could be factors. The origins of these constituents, and the conditions under which they are present, vary among the aquifers studied.

Dissolved Organic CarbonThe amount of DOC present in the water is not the only

determining factor in DBP formation potential. Although there is a semblance of a positive relation between concentrations of DOC and THMFP, using data for all wells (fig. 18), the two highest concentrations of THMFP (for water samples from

Coastal Plain wells) dominate, and the r2 for the entire data set is low (0.19). Linear relations are not apparent for the data points for wells grouped by aquifer type except those for wells completed in glacial aquifers. A stronger linear relation is pres-ent between UV-254 in untreated water and THMFP (shown in fig. 9), and the strongest relation is between UV-254 and total HAA concentration (fig. 19). Thus, it appears that the aromatic character of the DOC is an important factor in determining the DBP formation potential in ground water in New Jersey.

DOC in ground-water samples from the Coastal Plain is, for most samples, more aromatic than the DOC in samples from the bedrock and glacial aquifers, as indicated by SUVA calculations as well as the UV-254 measurements. The hydro-phobic fraction of DOC (DOC 3), which includes humic sub-stances, contains more aromatic compounds than the hydro-philic fraction. Concentrations of fraction DOC 3 were, in four of six samples from unconfined Coastal Plain aquifers, about twice as high as those in samples from bedrock or glacial aqui-fers (table 8). Higher concentrations of DBPs developed in the DOC 3 fractions in samples from the unconfined Coastal Plain

Table 1�. Concentrations of disinfection by-products in dissolved-organic-matter fractions in water samples from 20 community water-supply wells, New Jersey, 1998-99.

[BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; THMs, trihalomethanes; HAAs, haloacetic acids; HANS, haloaceto-nitriles; DOC, dissolved organic carbon; DOC 2, hydrophilic organic acids and neutrals and low-molecular-weight hydrophilic compounds fraction; DOC 3, hydrophobic organic acid fraction; DOC 6, hydrophilic organic acid fraction; µg/L, micrograms per liter; nf, no fraction isolated]

Total THMs Total HAAs Total HANs

USGS well

number

Aquifer type

DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)DOC �1

(µg/L)

030301 BR 22.0 nf 19.1 21.6 nf 13.7 0.0 nf 0.6030460 BR 16.1 nf 14.4 20.1 nf 18.2 0.0 nf 0.6130098 BR 12.7 nf 15.1 16.1 nf 8.4 0.2 nf 0.8210402 BR 16.5 nf 19.2 21.1 nf 11.5 0.2 nf 1.0350083 BR nf nf 15.2 nf nf 0.0 nf nf 2.4

270080 GL 21.8 nf 18.4 23.8 nf 12.7 0.2 nf 0.0270147 GL 35.2 nf 32.2 31.9 nf 20.6 0.4 nf 1.6270155 GL 15.7 nf 14.5 16.3 nf 10.8 0.3 nf 0.3270182 GL 9.6 nf 10.2 7.3 nf 8.7 nf nf 0.0390451 GL 15.6 nf 17.4 15.0 nf 8.8 0.3 nf 1.6

050039 CP 16.8 nf nf 12.0 nf nf 0.0 nf nf070177 CP 29.3 nf 29.4 26.0 nf 31.0 0.0 nf 0.0070368 CP 31.4 14.8 nf 35.3 8.8 nf 0.0 0.0 nf150207 CP 54.5 15.5 nf 44.7 14.5 nf 0.0 0.0 nf230195 CP 59.5 16.1 nf 67.1 16.9 nf 0.0 0.0 nf291264 CP 31.8 nf 26.1 22.6 nf 21.8 0.0 nf 0.0

010039 CCP 23.9 nf 11.3 27.7 nf 8.4 0.3 nf nf010600 CCP 32.9 nf 9.6 39.9 nf 7.4 0.0 nf 0.0090136 CCP 27.2 nf 17.8 30.7 nf 9.4 0.0 nf 0.7150276 CCP 31.9 nf 25.3 37.5 nf 16.0 0.0 nf 0.6

1 See table 6 and figure 3 for full description of each DOC fraction.

Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types �1

than in DOC 3 fractions in samples from bedrock and glacial aquifers. For samples from the unconfined Coastal Plain aqui-fers, relations of both total THMs and total HAAs in the DOC 3 fraction with SUVA were strong (r2 = 0.58 and 0.68, respec-tively). Overall, the data indicate that DOC, particularly the hydrophobic acids, in unconfined Coastal Plain ground water is more aromatic than those in water from the bedrock and glacial aquifers. Thus, for these ground waters, DOC with high aromaticity, presumably the hydrophobic fraction, appears to be an important precursor for DBP formation. Concentrations of THMs and HAAs in the DOC 3 fraction in water from the confined Coastal Plain aquifers also tended to be higher than those from bedrock and glacial aquifers, and were clearly higher than they were in the DOC 2 fraction (hydrophilic and neutral compounds) (table 13). Relations of THMs in samples from the confined Coastal Plain aquifers with SUVA show a virtually flat trend, although SUVA values, indicating aroma-ticity, for these samples are high. HAN development, on the other hand, was greater in the DOC 2 fraction than the DOC 3 fraction, although concentrations were much lower than those of the THMs and HAAs. Apparently, HAN development is not promoted by greater aromaticity.

Within the hydrophobic fraction, the proportions of aromatic and aliphatic compounds can vary substantially, arising from the origin of the DOC. Pomes and others (2000) indicate that aquatic humic substances with a predominance of aromatic compounds derive from terrestrial plant sources, and those with a predominance of aliphatic compounds derive from algal or bacterial sources. If most of the DOC present in ground water from a given aquifer is derived from materials within the aquifer matrix or matrixes through which recharge passes, then it appears likely that the age and geologic set-ting in which the aquifer materials were formed could have a bearing on how strong an effect DOC has as a precursor to DBP formation. Younger (Late Paleozoic to Cenozoic) sediments in which land-plant remains are present would be likely to contain water with more aromatic DOC and, prob-ably, a higher potential for DBP formation than older (early Paleozoic) sediments, particularly if the aquifers are confined. (DOC in water from aquifers composed of fractured igneous and metamorphic rocks would be derived only from the land surface in recharge.)

The aquifers sampled during the present study are all sedimentary in origin; the water samples with the highest DBP formation potentials (THMFP, total HAAs, and HANs), with few exceptions, come either from deep confined Coastal Plain aquifers or unconfined Coastal Plain aquifers (the Potomac-Raritan-Magothy and Kirkwood-Cohansey aquifer systems). The sediments of the Potomac-Raritan-Magothy aquifer system contain lignite; these identifiable plant remains occur as dispersed fragments and in thin layers, particularly in the upper part of the system. Sediments of the Kirkwood-Cohan-sey aquifer system contain fine-grained carbonaceous mate-rial, in dark-gray clays and dark, sometimes fossiliferous, silts (Owens and Sohl, 1969). Where the aquifer is confined, Lower Kirkwood sediments are overlain by a thick diatomaceous

clay bed (Zapecza, 1989). Plant material and phytoplankton would likely have been abundant in the marginal-marine (with the Mesozoic equivalent of mangrove swamps) and Cenozoic deltaic environments in which these Cretaceous and Tertiary sediments were deposited.

Only one well (270147) completed in a glacial aquifer yielded water with a comparably high DBP formation poten-tial. Some of the morainal deposits in northern New Jersey contain peat (Minard and Rhodehamel, 1969). Organic materi-als in sediment could supply precursor DOC for DBP forma-tion in water from parts of some of the glacial aquifers.

The other, obvious source of DOC in the unconfined aquifers is land-surface inputs to recharge from both natural and anthropogenic sources. Plant materials at land surface could be the major source of natural DOC in recharge waters. Anthropogenic sources of carbon compounds in recharge could include septic systems, composting facilities, and vari-ous land-surface and subsurface discharges of VOCs.

For those water samples from the 20 wells that contained detectable VOCs, neither MTBE nor PCE concentrations

Glacial


Bedrock


EXPLANATION

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83

WELL NUMBER

60

80

100

120

0

20

40

THM

FP, I

N M

ICRO

GRAM

S PE

R LI

TER

AQUIFER TYPE

Maximum contaminant level = 80 micrograms per liter

Figure 1�. Trihalomethane formation potential (THMFP) in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99.


showed any relation to THMFP. The highest concentrations of TCE were present in two samples with high THMFP, but rela-tions between TCE and THMFP were neither strongly positive nor linear. Although, it is possible that degradation of VOCs can contribute to DBP precursor carbon, it also is possible that the presence of VOCs only indicates that the ground water contains various constituents (which could include DOC) derived recently from the land surface.

Neither TOC nor DOC concentrations in water from the 20 community water-supply wells were related to depth to the top of the open interval of the wells or to well depth. Shallow wells (those completed at less than100 ft below land surface) and those with open intervals at shallow depths gener-ally yielded water with concentrations of carbon less than 1 mg/L, as did many of the deeper wells. In water from the unconfined aquifers, concentrations of TOC tended to increase with increasing depth to the open interval, and the highest concentrations of DOC were in water from wells completed at 115 and 282 ft (wells 270147 and 150207, respectively). It is likely that, were the organic carbon of mostly anthropogenic origin, water from the shallowest wells (or from those with open intervals at the shallowest depths) would contain higher

concentrations of DOC than would water from deep wells (or wells with deep open intervals), because shallow ground water in unconfined aquifers typically is more susceptible to con-tamination from the land surface than is deeper ground water. Although the water tapped by the wells in unconfined aquifers in this study contains constituents, mostly VOCs, that clearly are derived from human activities at the land surface, there is no unequivocal evidence of large inputs of DOC or TOC from the land surface to most of the wells in unconfined aquifers. Of the two wells (270147 and 150207) that yielded water with the highest concentration of DOC (1.4 mg/L), water from the former well contained several VOCs, some at concentrations exceeding MCLs. Water from the latter well contained a barely detectable level of 1,2-dichloroethane. A third well (070177) yielded water with 10 µg/L of cis-1.2-dichloroethylene and 43 µg/L of TCE, but the DOC in this water was only 0.70 mg/L. Consequently, DOC level is not a useful measure of the source of the DOC.

For most of the wells in unconfined aquifers, con-centrations of DOC generally appear to be typical of those determined previously for ground water in those aquifers. Consequently, although some inputs of organic carbon may be

Glacial


Bedrock


EXPLANATION

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83

WELL NUMBER

30

35

40

45

0

15

20

25

10

5

TOTA

L HA

As, I

N M

ICRO

GRAM

S PE

R LI

TER

AQUIFER TYPE

Figure 1�. Total haloacetic acids (HAAs) in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99. (Maximum contaminant level = 60 micrograms per liter)

Glacial


Bedrock


EXPLANATION

50

45

40

35

30

TOTA

L H

AA

CO

NCE

NTR

ATIO

N, I

N M

ICRO

GRA

MS

PER

LITE

RTHMFP, IN MICROGRAMS PER LITER

0 20 40 80

25

60

20

15

10

5

0120100

R2 = 0.65p-value = 0.000

AQUIFER TYPE

Figure 1�. Relation of total haloacetic acid concentration (HAA) to trihalomethane formation potential (THMFP) in treated water from 20 community water-supply wells in New Jersey, 1998-99.

Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types ��

anthropogenic, on the basis of the existing data, such inputs cannot be separated from naturally occurring organic carbon which, in some cases, is known to be substantial. In the case of water in the confined aquifers, all of the organic carbon in the water is derived from natural sources, because anthropogenic inputs to unconfined parts of the aquifers have had insufficient time to travel far downgradient beneath the overlying confin-ing units.

BromideConcentrations of bromide in source water to the 20 wells

varied substantially (fig. 20). In some cases, high concentra-tions (greater than 0.1 mg/L) likely were of anthropogenic origin—in particular, in water from well 030301, completed in a bedrock aquifer, where concentrations of sodium and chloride were highly elevated (209 and 634 mg/L, respec-tively). Concentrations of bromide in the confined aquifers, on the other hand, are natural. Concentrations of the brominated

THMs and HAAs in treated waters did not appear to be related to concentrations of bromide, however, with the exception of CHBr3. The concentrations of CHBr3 were higher in treated water from most of the wells in the bedrock aquifers than in treated water from most of the wells in the other aquifers (table 9). Source waters from the bedrock aquifers generally were as rich or richer in bromide as source water to wells in the other aquifers (fig. 20). Concentrations of the other bro-minated compounds commonly were higher in treated water from wells in Coastal Plain aquifers than in treated water from wells in the other aquifers. Thus, the magnitude of the bromide concentration is not the sole factor in formation of some of the brominated DBPs. Nevertheless, where concentrations of bromide either are high naturally, or are enhanced by anthro-pogenic inputs (as in water from well 030301), concentrations of CHBr3 are likely to be high in treated water.

Iron, Manganese, and AmmoniaMiller and others (1990) found, in a study of organic car-

bon and THMFP in Kansas aquifers, that THMFP was strongly

120

100

80

60

40

THM

FP, I

N M

ICRO

GRA

MS

PER

LITE

R


0.0 0.2 0.4 0.8

20

0.60

1.21.0 1.61.4

R2 = 0.19p-value = 0.054

Glacial


Bedrock


EXPLANATION

AQUIFER TYPE

Figure 18. Relation of dissolved organic carbon (DOC) concentration to trihalomethane formation potential (THMFP) in water from 20 community water-supply wells in New Jersey, 1998-99.

50

40

30

20

TOTA

L H

AA

CO

NCE

NTR

ATIO

N, I

N M

ICRO

GRA

MS

PER

LITE

R

UV-254, IN 1/CENTIMETERS

0.00 0.01 0.02

10

00.03 0.04

R2 = 0.60p-value = 0.000

Glacial


Bedrock


EXPLANATION

AQUIFER TYPE

Figure 19. Relation of total haloacetic acid (HAA) concentration to ultraviolet absorbance at 254 nanometers (UV-254) in water from 20 community water-supply wells in New Jersey, 1998-99.


related to ground-water concentrations of TOC, which, in turn, were related to concentrations of iron, manganese, and ammo-nia. Causes suggested for these relations include (1) reducing conditions under which less TOC was microbially metabo-lized, (2) presence of colloids with which TOC and the other three constituents are associated, and (3) complexation of iron and manganese by organic matter. In this study, concentrations of iron and manganese, which likely are derived mostly from minerals in the aquifers, varied by three orders of magnitude. The higher concentrations of iron and manganese typically occurred in water with low oxygen content. Concentrations of iron and manganese were not related to concentrations of TOC or DOC. Because the concentrations of iron and manganese reported in this study are for filtered samples, whereas the samples in the study of Miller and others (1990) apparently were not filtered, comparisons of results are viewed with cau-tion. Furthermore, in this study, ammonia was not detected in any water samples from the bedrock or glacial aquifers. For the water samples from the Coastal Plain aquifers, however, in which ammonia was detected, relations between concentra-tions of ammonia and DOC were positive (r2 = 0.58) (fig. 21) and similar to results from Miller and others (1990).

Nearly all of the ammonia + organic nitrogen measured in water samples from the Coastal Plain aquifers was ammo-

nia, whereas essentially none of the ammonia + organic nitro-gen measured in water samples from the bedrock and glacial aquifers was ammonia. The relation between organic carbon and ammonia in water from the Coastal Plain aquifers may be, in part, a result of the character of the organic carbon pres-ent in the ground water. In particular, in the confined Coastal Plain aquifers, the ammonia probably derives mostly from the microbial decomposition of organic matter in the aquifers. Brown coal (lignite), for example, can contain more than 5 weight-percent of nitrogen (Muller-Wegener, 1988); lignite is ubiquitous in sediments of the Potomac-Raritan-Magothy aquifer system of the New Jersey Coastal Plain. Most of the water samples from the Coastal Plain aquifers had low oxygen content; therefore, any inputs of nitrogen to the ground water at the sampling points would be in a reduced form, such as ammonia.

Reckow and others (1990) found a positive relation between organic N and production of Cl2AN. In this study, concentrations of ammonia + organic nitrogen for all wells showed only a weak positive relation with concentrations of total HANs (r2 = 0.17). Cl2AN developed in water from unconfined Coastal Plain wells, but there were insufficient

Glacial


Bedrock


EXPLANATION

2700

80

2701

47

2701

55

2701

82

3904

51

0500

39

0701

77

0703

68

1502

07

2301

95

2912

64

0100

39

0106

00

0901

36

1502

76

0303

01

0304

60

1300

98

2104

02

3500

83

WELL NUMBER

0.15

0.20

0.00

0.10

0.05

CON

CEN

TRAT

ION

OF

BROM

IDE,

IN M

ILLI

GRAM

S PE

R LI

TER

AQUIFER TYPE

Figure �0. Concentrations of bromide in water from 20 community water-supply wells in New Jersey, by aquifer type, 1998-99.



EXPLANATION

1.6

1.2

0.8

DO

C CO

NCE

NTR

ATIO

N, I

N M

ILLI

GRA

MS

PER

LITE

R

AMMONIA CONCENTRATION, IN MILLIGRAMS PER LITER AS N

0.0 0.4 0.8

0.4

0.0

1.2 1.6

R2 = 0.58p-value = 0.010

AQUIFER TYPE

Figure �1. Relation of concentrations of dissolved organic carbon (DOC) to concentrations of ammonia in water from 20 community water-supply wells in New Jersey Coastal Plain aquifers, 1998-99.

Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types ��

detections to draw any conclusions about relations with concentrations of ammonia + organic nitrogen. Using data for all 20 wells, the reduced species (ammonia + organic N) did not relate strongly to concentrations of THMs (r2 =0.10) either. The possibility that concentrations of the reduced nitrogen species might be higher as the aromatic content of the organic carbon increased was explored because the nitrogen in ammonia and amino compounds can become covalently linked to various aromatic structures (Anderson and others, 1989). Using the data for all 20 wells, the relation between UV-254 measurements and ammonia + organic nitrogen was not strong (r2 = 0.16). It was only slightly stronger for water from the unconfined Coastal Plain wells (r2 = 0.31). Relations between SUVA and ammonia + organic nitrogen were weaker than those between UV-254 measurements and ammonia + organic nitrogen.

Indicators of Disinfection By-Product Formation Potential

Overall, it appears that the aromatic character of the organic matter is an important factor in DBP production in the ground water sampled during this study. UV-254 measure-ments likely could be used to predict the potential of ground water to DBP formation upon chlorination because they would be indicative of both the magnitude of concentrations of DOC and the aromaticity of the DOC. Chemical constituents other than DOC appear to be poor indicators of DBP formation potential. Nevertheless, because the pHs of the treated water samples in this study were adjusted to 7 before chlorination, relations between THMFP and various constituents may be different for waters chlorinated prior to pH adjustment.

The presence of ammonia in source water to the wells in the Coastal Plain aquifers raises the issue of the effectiveness of chlorination. Reactions between chlorine and ammonia result in compounds that are less effective as disinfectants, although this can be overcome by increases in the chlorine dose (McClanahan, 1977).

Summary and ConclusionsWater samples were collected from 20 community water-

supply wells in New Jersey, of which 16 were completed in unconfined bedrock, glacial, and Coastal Plain aquifers, and 4 were completed in confined Coastal Plain aquifers. The samples were analyzed for major and minor ions, selected trace elements, total organic carbon (TOC), dissolved organic carbon (DOC), and volatile organic compounds (VOCs). DOC fractions were determined. Raw water samples were chlo-rinated, the pH adjusted to 7, and analyzed for the common groups of disinfection by-products (DBPs): trihalomethanes (THMs), haloacetic acids (HAAs), and haloacetonitriles (HANs) after incubation for 168 hours (7 days). Selected chlo-rinated samples also were incubated for 6 and 24 hours.

Water from all wells completed in unconfined aquifers contained one or more VOCs, some at concentrations exceed-ing maximum contaminant levels (MCL). High concentra-tions of sodium, chloride, and sulfate were present in water samples from several wells completed in unconfined aquifers at levels exceeding secondary maximum contaminant levels (SMCLs) of 50, 250, and 250 mg/L, respectively. Although the high levels of sulfate were natural, the high concentrations of sodium and chloride were indicative of anthropogenic inputs to ground water.

Concentrations of nitrate exceeding 1 mg/L as N were present in samples from most of the wells in bedrock and glacial aquifers, although none exceeded the MCL of 10 mg/L as N. Because water from most of the Coastal Plain wells had low oxygen contents, no nitrate was detected in samples from several wells completed in unconfined Coastal Plain aquifers and all wells completed in confined Coastal Plain aquifers. Water from all wells completed in the Coastal Plain aquifers contained detectable concentrations of ammonia, however.

Water from the 20 wells was chlorinated and incubated for 7 days. With few exceptions, higher concentrations of DBPs were formed in water from the wells in Coastal Plain aquifers than in water from wells in bedrock or glacial aqui-fers. A positive relation was observed between the formation potentials for the classes of DBPs and the aromaticity of the precursor DOC, as estimated by measurements of ultraviolet absorption at 254 nanometers. Water samples from seven selected wells were chlorinated and incubated for 6, 24, and 168 hours. Water from Coastal Plain wells, in general, devel-oped higher concentrations of THMs, HAAs, and HANs than did the samples from bedrock and glacial aquifers. Rates of formation were variable.

DOC in water samples was fractionated to determine hydrophobic and hydrophilic fractions. DOC in water from the wells in Coastal Plain aquifers contained, in some cases, slightly larger concentrations of hydrophobic organic acids than did DOC in water from wells in the bedrock and glacial aquifers. When treated with chlorine, both the hydrophobic and hydrophilic acid fractions developed DBPs. Concentra-tions of THMs and HAAs generally were higher in the hydro-phobic fraction of DOC from Coastal Plain aquifers than in the same fractions from bedrock and glacial aquifers.

DOC in water from wells in unconfined aquifers may derive partly from the VOCs that are present, but concentra-tions of DOC in most of these water samples were typical of DOC levels in the unconfined aquifers. Water from one well in a glacial aquifer contained several VOCs, some at concen-trations exceeding MCLs, and the concentration of DOC was high relative to concentrations in samples from most other wells. Another well in an unconfined Coastal Plain aquifer yielded water with an equally high concentration of DOC, but only one VOC was detected at a low concentration. The sediments of the Coastal Plain aquifers contain substantial amounts of organic matter that can contribute aromatic DOC compounds to the ground water. Thus, much of the DOC in water from the wells in unconfined Coastal Plain aquifers


probably was natural. The DOC in water from the wells in the confined Coastal Plain aquifers was wholly natural in origin, as the wells are too far downgradient beneath confining units to receive anthropogenic inputs.

Organic material is present in some of the sedimentary rocks of the bedrock aquifers, but it may not be readily incor-porated into the ground water. Organic matter in the unconsol-idated materials of the glacial aquifers probably occurs sporad-ically. The geologic characteristics of the aquifers do appear to be an important factor in the supply of organic carbon to the ground water, and thus can play a role in the potential of ground water to form DBPs when chlorinated.

AcknowledgmentsThe authors thank the water purveyors for allowing

access to their wells and express appreciation to Judy Louis of NJDEP for assistance with study design. Thanks are due also to USGS colleagues: George R. Aiken for his guidance in fractionation techniques, and Jacob Gibs and Gary K. Speiran for insightful comments that greatly improved the manuscript.

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Appendixes

App

endi

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ality

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cial

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Appendixes �1

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<0.0

1<0

.05

0.01

<0.1

nd21

0402

<0.0

2<0

.10

<10

<2.2

<0.3

<0.2

9<0

.1<0

.01

<0.0

1<0

.05

<0.0

10.

3nd

0901

36<0

.02

<0.1

0<1

0<4

.0<0

.1<0

.1<0

.1<0

.01

<0.0

1<0

.05

<0.0

10.

1nd


App

endi

x 1-

1 Qu

ality

-ass

uran

ce d

ata

(bla

nks,

repl

icat

es, a

nd re

late

d en

viro

nmen

tal s

ampl

es) f

or w

ater

sam

ples

from

com

mun

ity w

ater

-sup

ply

wel

ls, N

ew J

erse

y, 1

998-

99.—

Cont

inue

d

USG

S w

ell

num

ber

Dis

solv

ed

solid

s (m

g/L)

(�

0�01

)

Ben

zene

(µ

g/L)

(�

�0�0

)

Bro

mo-

dich

loro

-m

etha

ne

(µg/

L)

(��1

01)

Bro

mo-

form

(µ

g/L)

(�

�10�

)

Carb

on

tetr

a-ch

lori

de

(µg/

L)

(��1

0�)

Chlo

ro-

benz

ene

(µg/

L)

(��

01)

Chlo

rofo

rm

(µg/

L)

(��1

0�)

Dib

rom

o-ch

loro

-m

etha

ne

(µg/

L)

(��1

0�)

1,�-

Dic

hlor

o-be

nzen

e (µ

g/L)

(�

��

)

1,�-

Dic

hlor

o-be

nzen

e (µ

g/L)

(�

��

)

1,�-

Dic

hlor

o-be

nzen

e (µ

g/L)

(�

��1

)

Dic

hlor

o-di

fluor

o-m

etha

ne

(µg/

L)

(��

�8)

1,1-

Dic

hlor

o-et

hane

(µ

g/L)

(�

��9�

)

2104

0232

5<0

.10

<0.0

5<0

.10

<0.0

9<0

.03

E0.0

5<0

.2<0

.05

<0.0

5<0

.05

<0.1

4<0

.07

2104

0233

1<0

.10

<0.0

5<0

.10

<0.0

9<0

.03

E0.0

5<0

.2<0

.05

<0.0

5<0

.05

<0.1

4<0

.07

2701

5538

7<0

.04

E0.0

4<0

.06

<0.0

6<0

.03

4.10

<0.2

<0.0

5<0

.05

<0.0

5<0

.27

E0.0

527

0155

391

<0.0

4E0

.03

<0.0

6<0

.06

<0.0

33.

98<0

.2<0

.05

<0.0

5<0

.05

<0.2

7E0

.05

0701

7720

4<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.207

0177

203

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

0100

3910

9<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.201

0039

110

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

3500

83nd

<0.0

4<0

.05

<0.0

6<0

.06

<0.0

3<0

.05

<0.2

<0.0

5<0

.05

<0.0

5<0

.27

<0.0

723

0195

nd<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.221

0402

nd<0

.10

<0.0

5<0

.10

<0.0

9<0

.03

<0.0

5<0

.2<0

.05

<0.0

5<0

.05

<0.1

4<0

.07

0901

36nd

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

Appendixes ��

App

endi

x 1-

1 Qu

ality

-ass

uran

ce d

ata

(bla

nks,

repl

icat

es, a

nd re

late

d en

viro

nmen

tal s

ampl

es) f

or w

ater

sam

ples

from

com

mun

ity w

ater

-sup

ply

wel

ls, N

ew

Jers

ey, 1

998-

99.—

Cont

inue

d

USG

S w

ell

num

ber

1,�-

Dic

hlor

o-et

hane

(µ

g/L)

(�

�10�

)

1,1-

Dic

hlor

o-et

hyle

ne

(µg/

L)

(��

01)

cis-

1,�-

Dic

hlor

o-et

hyle

ne

(µg/

L)

(��0

9�)

tran

s-1,

�-D

ichl

oro-

ethy

lene

(µ

g/L)

(�

��

)

1,�-

Dic

hlor

o-pr

opan

e (µ

g/L)

(�

��1

)

Ethy

l-be

nzen

e (µ

g/L)

(�

��1

)

Met

hyle

ne

chlo

ride

(µ

g/L)

(�

��

)

Met

hyl

tert

-but

yl

ethe

r (µ

g/L)

(�

80��

)

Styr

ene

(µg/

L)

(��1

�8)

Tetr

achl

ro-

ethy

lene

(µ

gL)

(��

��)

Tolu

ene

(µg/

L)

(��0

10)

1,1,

1-Tr

i-ch

loro

-et

hane

(µ

g/L)

(�

��0�

)

Tric

hlor

o-et

hyle

ne

(µg/

L)

(�91

80)

2104

02<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

M<0

.04

<0.1

0<0

.05

<0.0

3<0

.04

2104

02<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

M<0

.04

<0.1

0<0

.05

<0.0

3<0

.04

2701

55<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

0.7

<0.0

4<0

.10

<0.0

50.

25<0

.04

2701

55<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

0.7

<0.0

4<0

.10

<0.0

50.

26<0

.04

0701

772.

9<0

.210

.0<0

.2<0

.2<0

.2<0

.2<0

.2<0

.21.

9<0

.2<0

.243

.007

0177

3<0

.210

.4<0

.2<0

.2<0

.2<0

.2<0

.2<0

.22

<0.2

<0.2

40.0

0100

39<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.201

0039

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

3500

83<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

<0.2

<0.0

4<0

.10

E0.0

8<0

.03

<0.0

423

0195

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

2104

02<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

<0.2

<0.0

4<0

.10

E0.0

2<0

.03

<0.0

409

0136

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

App

endi

x 1-

1 Qu

ality

-ass

uran

ce d

ata

(bla

nks,

repl

icat

es, a

nd re

late

d en

viro

nmen

tal s

ampl

es) f

or w

ater

sa

mpl

es fr

om c

omm

unity

wat

er-s

uppl

y w

ells

, New

Jer

sey,

199

8-99

.—Co

ntin

ued

USG

S w

ell

num

ber

Tric

hlor

o-flu

oro-

met

hane

(µ

g/L)

(�

��88

)

Viny

l ch

lori

de

(µg/

L)

(�91

��)

m, p

-Xy

lene

(µ

g/L)

(8

��9�

)

o-Xy

lene

(µ

g/L)

(�

�1��

)

Xyle

ne

(µg/

L)

(81�

�1)

2104

02<0

.09

<0.1

<0.0

6<0

.06

nd21

0402

<0.0

9<0

.1<0

.06

<0.0

6nd

2701

550.

18<0

.1<0

.06

<0.0

4nd

2701

550.

18<0

.1<0

.06

<0.0

4nd

0701

77<0

.2<0

.2nd

nd<0

.207

0177

<0.2

<0.2

ndnd

<0.2

0100

39<0

.2<0

.2nd

nd<0

.201

0039

<0.2

<0.2

ndnd

<0.2

3500

83<0

.09

<0.1

<0.0

6<0

.04

nd23

0195

<0.2

<0.2

ndnd

<0.2

2104

02<0

.09

<0.1

<0.0

6<0

.06

nd09

0136

<0.2

<0.2

ndnd

<0.2


App

endi

x 1-

� Qu

ality

-ass

uran

ce d

ata

(bla

nks,

repl

icat

es, a

nd re

late

d en

viro

nmen

tal s

ampl

es) f

or c

hlor

inat

ed w

ater

sam

ples

from

com

mun

ity w

ater

-sup

ply

wel

ls, N

ew

Jers

ey, 1

998-

99.

[BR

, bed

rock

; GL,

gla

cial

; CP,

unc

onfin

ed C

oast

al P

lain

; CC

P, c

onfin

ed C

oast

al P

lain

; mg/

L, m

illig

ram

s per

lite

r; µg

/L, m

icro

gram

s per

lite

r; nd

, no

data

; <, l

ess t

han.

Num

ber i

n pa

rent

hese

s is p

aram

eter

co

de u

sed

to id

entif

y th

e co

nstit

uent

, pro

perty

, or c

hara

cter

istic

in th

e U

.S. G

eolo

gica

l Sur

vey

Nat

iona

l Wat

er In

form

atio

n Sy

stem

(NW

IS) d

atab

ase.

]

USG

S w

ell

num

ber

Aqu

ifer

type

Dat

e co

llect

edTi

me

colle

cted

Sam

ple

type

Incu

-ba

tion

time

(hou

rs)

Chlo

rine

do

se

(mg/

L)

(99�

00)

Chlo

rine

re

sidu

al

(mg/

L)

(99�

01)

Chlo

rate

(m

g/L)

(9

9��0

)

Bro

mo-

dich

loro

-m

etha

ne

(µg/

L)

(99�

0�)

Bro

mo-

form

(µ

g/L)

(9

9�0�

)

Chlo

ro-

form

(µ

g/L)

(9

9�0�

)

Dib

rom

o-ch

loro

-m

etha

ne

(µg/

L)

(99�

0�)

Chlo

ral

hydr

ate

(µg/

L)

(99�

�1)

Bro

mo-

chlo

ro-

acet

ic

acid

(µg/

L)

(99�

��)

2104

02B

R09

/15/

9990

0En

viro

nmen

tal

168

55

1,80

06.

73.

74.

96.

31.

53.

221

0402

BR

09/1

5/99

901

Rep

licat

e16

85

51,

800

6.4

44.

66.

21.

73.

327

0155

GL

09/1

6/99

900

Envi

ronm

enta

l16

85

41,

800

5.8

2.5

7.5

5.4

1.8

2.3

2701

55G

L09

/16/

9990

1R

eplic

ate

168

55

1,90

05

2.4

6.9

4.9

1.3

1.7

0701

77C

P07

/24/

9890

0En

viro

nmen

tal

168

104

1,60

015

117

7.1

2.7

3.1

0701

77C

P07

/24/

9890

1R

eplic

ate

168

104

1,70

014

116

6.9

2.3

4.1

0100

39C

CP

07/2

8/98

900

Envi

ronm

enta

l16

8nd

nd

850

8.6

0.2

313.

2<0

.13.

401

0039

CC

P07

/28/

9890

1R

eplic

ate

168

7.5

4

790

8.8

0.2

323.

4<0

.13.

235

0083

BR

10/1

2/99

1005

Bla

nk16

85

42,

000

<0.1

<0.1

3<0

.13.

7<0

.123

0195

CP

07/2

1/98

1005

Bla

nk16

87.

56

9

5<0

.1<0

.16.

8<0

.112

01.

121

0402

BR

09/1

4/99

905

Bla

nk16

85

42,

100

0.8

<0.1

4.8

0.1

5.8

<0.1

0901

36C

CP

08/2

7/98

1005

Bla

nk16

87.

54

59

0<0

.1<0

.10.

7<0

.11.

2<0

.1

Appendixes ��

App

endi

x 1-

� Qu

ality

-ass

uran

ce d

ata

(bla

nks,

repl

icat

es, a

nd re

late

d en

viro

nmen

tal s

ampl

es) f

or c

hlor

inat

ed w

ater

sam

ples

from

com

mun

ity w

ater

-sup

ply

wel

ls,

New

Jer

sey,

199

8-99

.—Co

ntin

ued

USG

S w

ell

num

ber

Aqu

ifer

type

Dib

rom

o-ac

etic

ac

id

(µg/

L)

(99�

1�)

Dic

hlor

o-ac

etic

ac

id

(µg/

L)

(99�

09)

Mon

o-ch

loro

-ac

etic

ac

id (µ

g/L)

(9

9�08

)

Tric

hlor

o-ac

etic

ac

id

(µg/

L)

(99�

10)

Dic

hlor

o-ac

eto-

nitr

ile

(µg/

L)

(99�

1�)

Bro

mo-

chlo

ro-

acet

onitr

ile

(µg/

L)

(99�

1�)

Dib

rom

o-ac

eto-

nitr

ile

(µg/

L)

(99�

1�)

Tric

hlor

o-ac

eto-

nitr

ile

(µg/

L)

(99�

1�)

Chlo

ro-

picr

in

(µg/

L)

(99�

19)

1,1,

1-Tr

ichl

oro-

�-pr

opan

one

(µg/

L)

(99�

1�)

1,1-

Dic

hlor

o-�-

prop

anon

e (µ

g/L)

(9

9�18

)

2104

02B

R3.

73.

23.

81.

7<0

.10.

61.

0<0

.1nd

ndnd

2104

02B

R4.

13

<0.1

1.8

<0.1

0.6

1.1

<0.1

ndnd

nd27

0155

GL

2.5

2.1

2.8

1.7

<0.1

0.6

0.9

<0.1

ndnd

nd27

0155

GL

1.9

1.2

<0.1

1.2

<0.1

0.6

<0.1

<0.1

ndnd

nd07

0177

CP

1.4

6.9

<0.1

4.0

<0.1

<0.1

1.1

<0.1

ndnd

nd07

0177

CP

29.

2<0

.15.

4<0

.1<0

.11

<0.1

ndnd

nd

0100

39C

CP

<0.1

14<0

.118

.0<0

.1<0

.1<0

.1<0

.1nd

ndnd

0100

39C

CP

<0.1

14<0

.116

<0.1

<0.1

<0.1

<0.1

ndnd

nd35

0083

BR

<0.1

1.9

<0.1

3.3

<0.1

<0.1

<0.1

<0.1

ndnd

nd23

0195

CP

<0.1

3<0

.11.

8<0

.1<0

.1<0

.1<0

.1nd

ndnd

2104

02B

R<0

.12.

94.

13.

4<0

.1<0

.1<0

.1<0

.1nd

nd0.

509

0136

CC

P<0

.1<0

.1<0

.1<0

.1<0

.1<0

.1<0

.1<0

.1nd

ndnd


App

endi

x �

Cons

titue

nt c

once

ntra

tions

in, a

nd c

hara

cter

istic

s of

, wat

er s

ampl

es fr

om 2

0 co

mm

unity

wat

er-s

uppl

y w

ells

, New

Jer

sey

1998

-99.

[BR

CKS

, Bru

nsw

ick;

PSS

C, P

assa

ic; S

CKN

, Sto

ckto

n; S

FDF,

Stra

tifie

d D

rift;

MR

PAU

, Upp

er P

otom

ac-R

arita

n-M

agot

hy; M

RPA

M, M

iddl

e Po

tom

ac-R

arita

n-M

agot

hy; M

RPA

L, L

ower

Pot

omac

-Rar

itan-

Mag

othy

; OD

BG, O

ldbr

idge

; C

KKD

, Kirk

woo

d-C

ohan

sey;

KR

KDL,

Low

er K

irkw

ood;

BR

, bed

rock

; GL,

gla

cial

; CP,

unc

onfin

ed C

oast

al P

lain

; CC

P, c

onfin

ed C

oast

al P

lain

; Lab

, lab

orat

ory;

AN

C, a

cid-

neut

raliz

ing

capa

city

; µS/

cm, m

icro

siem

ens

per c

entim

eter

at

25o C

elsi

us; o C

, deg

rees

Cel

sius

; mg/

L, m

illigr

ams

per l

iter;

µg/L

, mic

rogr

ams

per l

iter,

nd, n

o da

ta; <

, les

s th

an; E

, est

imat

ed; M

, pre

senc

e ve

rifie

d bu

t not

qua

ntifi

ed. N

umbe

r in

pare

nthe

ses

is p

aram

eter

cod

e us

ed to

iden

tify

the

cons

titue

nt, p

rope

rty, o

r cha

ract

eris

tic in

the

U.S

. Geo

logi

cal S

urve

y N

atio

nal W

ater

Info

rmat

ion

Syst

em (N

WIS

) dat

abas

e.]

USG

S w

ell

num

ber

Aqu

ifer

code

Aqu

ifer

type

Dat

e sa

mpl

edSt

atio

n id

entif

i-ca

tion

num

ber

Fiel

d al

ka-

linity

(m

g/L

as

CaCO

�) (�

908�

)

Lab

AN

C (m

g/L

as

CaCO

�) (9

0�10

)

Dis

solv

ed

oxyg

en

(mg/

L)

(00�

00)

Fiel

d pH

(0

0�00

)

Lab

pH

(00�

0�)

Spec

ific

cond

uc-

tanc

e (µ

S/cm

) (0

009�

)

Lab

spec

ific

cond

uc-

tanc

e (µ

S/cm

) (9

009�

)

Tem

per-

atur

e (o C)

(0

0100

)

Dis

solv

ed

orga

nic

carb

on

(mg/

L)

(00�

81)

Tota

l or

gani

c ca

rbon

(m

g/L)

(0

0�80

)

0303

0122

7BR

CK

SB

R09

/22/

9941

0046

0740

7470

116

016

61.

87.

77.

52,

250

2,26

012

.50.

20.

403

0460

227P

SSC

BR

09/2

2/99

4055

4007

4081

601

189

200

5.3

7.3

7.1

69

7

697

14.5

0.9

0.3

1300

9822

7PSS

CB

R09

/21/

9940

4534

0741

4020

118

119

53.

47.

37.

2

956

94

313

.40.

90.

521

0402

231S

CK

NB

R09

/15/

9940

1936

0743

9300

520

621

83.

06.

86.

9

575

57

113

.91.

01.

035

0083

227P

SSC

BR

10/0

7/99

4035

5707

4275

503

131

133

1.2

7.4

7.4

1,45

01,

430

12.9

0.6

0.5

2700

8011

2SFD

FG

L09

/20/

9940

5414

0743

1090

114

515

52.

17.

87.

5

589

59

411

.90.

70.

527

0147

112S

FDF

GL

09/2

0/99

4048

5607

4233

901

196

206

0.1

7.9

7.8

68

5

686

12.4

1.4

1.2

2701

5511

2SFD

FG

L09

/16/

9940

5018

0742

7450

114

915

70.

67.

37.

3

713

71

014

.10.

60.

627

0182

112S

FDF

GL

09/2

1/99

4051

1107

4231

001

134

138

1.3

8.1

7.8

38

2

390

12.1

0.4

E0.2

3904

5111

2SFD

FG

L09

/23/

9940

4248

0741

8520

217

418

53.

37.

47.

4

663

65

412

.90.

80.

4

0500

3921

1MR

PAM

CP

07/2

8/98

4004

0407

4552

001

3738

3.1

5.7

6.1

27

5

280

13.4

0.5

0.7

0701

7721

1MR

PAL

CP

07/2

4/98

3955

2107

5043

501

5845

0.1

5.9

6.3

34

7

344

14.0

0.7

1.0

0703

6821

1MR

PAL

CP

07/2

7/98

3958

4807

5034

701

7161

0.1

6.5

6.7

25

5

245

15.2

1.1

1.0

1502

0721

1MR

PAL

CP

07/2

9/98

3951

5607

5105

301

146

145

0.1

6.4

6.7

39

9

385

13.4

1.4

1.4

2301

9521

1OD

BG

CP

07/2

2/98

4025

3707

4200

201

<1<1

0.1

4.8

5.1

25

8

259

14.6

1.0

1.2

2912

6412

1CK

KD

CP

07/2

3/98

4005

0007

4045

501

<14

2.5

4.7

5.0

18

4

185

13.2

0.8

0.9

0100

3912

2KR

KD

LC

CP

07/2

8/98

3923

2407

4231

401

4953

0.1

6.7

7.3

14

3

149

18.2

0.4

0.6

0106

0012

2KR

KD

LC

CP

07/3

0/98

3920

4507

4284

001

4554

0.1

7.0

7.7

14

2

149

18.6

0.4

0.6

0901

3612

2KR

KD

LC

CP

07/3

1/98

3911

5207

4392

701

8378

0.1

7.7

8.1

20

3

212

18.8

0.5

0.5

1502

7621

1MR

PAU

CC

P07

/27/

9839

4821

0751

0260

112

812

80.

17.

78.

1

382

37

914

.40.

70.

8

Appendixes ��

App

endi

x �

Cons

titue

nt c

once

ntra

tions

in, a

nd c

hara

cter

istic

s of

, wat

er s

ampl

es fr

om 2

0 co

mm

unity

wat

er-s

uppl

y w

ells

, New

Jer

sey

1998

-99.

—Co

ntin

ued

USG

S w

ell

num

ber

Silic

a (m

g/L)

(0

09��

)

Har

dnes

s (m

g/L

as

CaCO

�) (0

0900

)

Dis

solv

ed

solid

s (m

g/L)

(�

0�01

)

Ben

zene

(µ

g/L)

(�

�0�0

)

Bro

mod

i-ch

loro

-m

etha

ne

(µg/

L)

(��1

01)

Bro

mo-

form

(µ

g/L)

(�

�10�

)

Carb

on

tetr

a-ch

lori

de

(µg/

L)

(��1

0�)

Chlo

ro-

benz

ene

(µg/

L)

(��

01)

Chlo

rofo

rm

(µg/

L)

(��1

0�)

Dib

rom

o-ch

loro

-m

etha

ne

(µg/

L)

(��1

0�)

1,�-

Dic

hlo-

robe

nzen

e (µ

g/L)

(�

��

)

1,�-

Dic

hlo-

robe

nzen

e (µ

g/L)

(�

��

)

1,�-

Dic

hlo-

robe

nzen

e (µ

g/L)

(�

��1

)

0303

0115

.854

01,

180

<0.0

4<0

.05

<0.0

6<0

.06

<0.0

30.

24<0

.2<0

.05

<0.0

5<0

.05

0304

6018

.927

0

396

E0.0

1E0

.04

<0.0

6E2

.27

<0.0

32.

41<0

.2<0

.05

<0.0

5<0

.05

1300

9823

.937

0

531

<0.0

4<0

.05

<0.0

60.

33<0

.03

0.93

<0.2

<0.0

5<0

.05

<0.0

521

0402

24.5

270

32

5<0

.1<0

.05

<0.1

<0.0

9<0

.03

E0.0

5<0

.2<0

.05

<0.0

5<0

.05

3500

8319

.677

01,

110

<0.0

4<0

.05

<0.0

6<0

.06

<0.0

30.

26<0

.2<0

.05

<0.0

5<0

.05

2700

8024

.723

0

324

<0.0

4<0

.05

<0.0

6<0

.06

<0.0

3E0

.08

<0.2

<0.0

5<0

.05

<0.0

527

0147

25.5

280

39

4<0

.04

<0.0

5<0

.06

<0.0

6<0

.03

E0.0

7<0

.2<0

.05

<0.0

5<0

.05

2701

5527

.329

0

387

<0.0

4E0

.04

<0.0

6<0

.06

<0.0

34.

10<0

.2<0

.05

<0.0

5<0

.05

2701

8221

.918

0

228

<0.0

4<0

.05

<0.0

6E0

.03

<0.0

3E0

.05

<0.2

<0.0

5<0

.05

<0.0

539

0451

24.5

280

37

8<0

.04

<0.0

5<0

.06

<0.0

6<0

.03

0.44

<0.2

<0.0

5<0

.05

<0.0

5

0500

3910

.078

15

0<0

.20.

5<0

.2<0

.2<0

.237

.9<0

.2<0

.2<0

.2<0

.207

0177

13.1

130

20

4<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.207

0368

6.4

65

138

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

1502

0713

.084

21

9<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.223

0195

6.1

38nd

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

2912

645.

633

10

10.

5<0

.2<0

.2<0

.2<0

.20.

8<0

.20.

30.

30.

301

0039

32.6

21

109

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

0106

0031

.323

10

5<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.209

0136

19.9

31

136

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

1502

768.

733

21

6<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2


App

endi

x �

Cons

titue

nt c

once

ntra

tions

in, a

nd c

hara

cter

istic

s of

, wat

er s

ampl

es fr

om 2

0 co

mm

unity

wat

er-s

uppl

y w

ells

, New

Jer

sey

1998

-99.

—Co

ntin

ued

USG

S w

ell

num

ber

Dic

hlor

o-di

fluor

o-m

etha

ne

(µg/

L)

(��

�8)

1,1-

Dic

hlor

o-et

hane

(µ

g/L)

(�

��9�

)

1,�-

Dic

hlor

o-et

hane

(µ

g/L)

(�

�10�

)

1,1-

Dic

hlor

o-et

hyle

ne

(µg/

L)

(��

01)

cis-

1,�-

Dic

hlor

o-et

hyle

ne

(µg/

L)

(��0

9�)

tran

s-1,

�-D

ichl

oro-

ethy

lene

(µ

g/L)

(�

��

)

1,�-

Dic

hlor

o-pr

opan

e (µ

g/L)

(�

��1

)

Ethy

l-be

nzen

e (µ

g/L)

(�

��1

)

Met

hyle

ne

chlo

ride

(µ

g/L)

(�

��

)

Met

hyl

tert

bu

tyl

ethe

r (µ

g/L)

(�

80��

)

Styr

ene

(µg/

L)

(��1

�8)

Tetr

achl

oro-

ethy

lene

(µ

g/L)

(�

��

)

Tolu

ene

(µg/

L)

(��0

10)

0303

01<0

.27

0.27

<0.1

0.17

0.13

<0.0

3<0

.07

<0.0

3<0

.40.

9<0

.04

4.00

<0.0

503

0460

<0.2

70.

15<0

.10.

15E0

.05

<0.0

3<0

.07

<0.0

3<0

.41.

3<0

.04

23.0

<0.0

513

0098

E0.1

80.

13<0

.1E0

.06

1.32

E0.0

1<0

.07

<0.0

3<0

.44.

3<0

.04

19.4

<0.0

521

0402

<0.1

4<0

.07

<0.1

<0.0

4<0

.04

<0.0

3<0

.07

<0.0

3<0

.4M

<0.0

4<0

.1<0

.05

3500

83<0

.27

0.14

<0.1

0.18

0.63

<0.0

3<0

.07

<0.0

3<0

.4E0

.1<0

.04

1.86

<0.0

5

2700

80<0

.27

1.06

<0.1

0.26

0.38

<0.0

3<0

.07

<0.0

3<0

.40.

2<0

.04

E0.0

8<0

.05

2701

47<0

.27

0.79

<0.1

0.42

1.90

E0.0

2<0

.07

<0.0

3<0

.41.

6<0

.04

E0.0

8<0

.05

2701

55<0

.27

E0.0

5<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

0.7

<0.0

4<0

.1<0

.05

2701

82E0

.03

<0.0

7<0

.1E0

.02

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

E0.1

<0.0

4<0

.1<0

.05

3904

51<0

.27

<0.0

7<0

.1<0

.04

<0.0

4<0

.03

<0.0

7<0

.03

<0.4

E0.1

<0.0

40.

26<0

.05

0500

39<0

.20.

5<0

.2<0

.22.

0<0

.2<0

.2<0

.2<0

.20.

6<0

.2<0

.2<0

.207

0177

<0.2

<0.2

2.9

<0.2

10.0

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

1.9

<0.2

0703

68<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.20.

9<0

.2<0

.2<0

.215

0207

<0.2

<0.2

0.4

<0.2

<0.2

<0.2

0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

2301

95<0

.2<0

.20.

3<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2

2912

64<0

.20.

5<0

.2<0

.20.

3<0

.2<0

.2<0

.2<0

.22.

6<0

.2<0

.2<0

.201

0039

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

0106

00<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.209

0136

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

<0.2

1502

76<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2<0

.2

Appendixes �9

App

endi

x �

Cons

titue

nt c

once

ntra

tions

in, a

nd c

hara

cter

istic

s of

, wat

er s

ampl

es fr

om 2

0 co

mm

unity

wat

er-s

uppl

y w

ells

, New

Jer

sey

1998

-99.

—Co

ntin

ued

USG

S w

ell

num

ber

Calc

ium

(m

g/L)

(0

091�

)

Mag

nesi

um

(mg/

L)

(009

��)

Sodi

um

(mg/

L)

(009

�0)

Pota

s-si

um

(mg/

L)

(009

��)

Am

mon

ia

(mg/

L as

N)

(00�

08)

Am

mon

ia

+ or

gani

c ni

trog

en

(mg/

L as

N)

(00�

��)

Iron

(µ

g/L)

(0

10��

)

Man

g-an

ese

(µg/

L)

(010

��)

Sulfa

te

(mg/

L)

(009

��)

Chlo

ride

(m

g/L)

(0

09�0

)

Fluo

ride

(m

g/L)

(0

09�0

)

Bro

mid

e (m

g/L)

(�

18�0

)

Nitr

ite

(mg/

L as

N)

(00�

1�)

Nitr

ite +

ni

trat

e (m

g/L

as N

) (0

0��1

)

Ort

ho-

phos

phat

e (m

g/L

as P

) (0

0��1

)

0303

0111

561

.620

92.

01<0

.02

<0.1

0

<10

E

1.8

31.

563

4<0

.10.

19<0

.010

2.47

0.01

0304

6079

.217

.728

.83.

87<0

.02

E0.0

7

<10

E

2.1

32.

1 7

4.0

<0.1

0.06

<0.0

104.

860.

0113

0098

121

17.1

36.8

1.55

<0.0

2<0

.10

<1

0

<2.

2 5

5.7

150

<0.1

0.18

<0.0

103.

630.

0321

0402

68.2

23.0

15.9

1.67

<0.0

2E0

.08

<1

0

<2.

2 2

2.3

40.

7<0

.10.

08<0

.010

1.04

0.05

3500

8327

122

.739

.21.

54<0

.02

E0.0

9

<10

<

2.2

623

36.

70.

20.

10<0

.010

2.95

0.03

2700

8052

.823

.725

.21.

82<0

.02

<0.1

0 <

10

3

.1 2

3.8

78.

5<0

.10.

05<0

.01

1.49

0.03

2701

4768

.026

.529

.81.

34<0

.02

E0.0

6

E 6

39

0 5

9.4

64.

5<0

.10.

040.

028

0.17

0.08

2701

5573

.826

.321

.91.

39<0

.02

E0.0

7

E 8

3.6

22.

911

3<0

.10.

05<0

.010

2.34

0.02

2701

8244

.315

.98.

060.

89<0

.02

<0.1

0

23

<

2.2

20.

6 2

7.6

<0.1

0.06

<0.0

100.

730.

1039

0451

85.0

16.0

23.2

1.18

<0.0

2E0

.09

<1

0

<2.

2 3

9.0

73.

2<0

.10.

09<0

.010

2.54

0.02

0500

3914

.79.

9316

.93.

650.

360.

35

<10

1

6.1

29.

5 2

8.4

<0.1

0.04

<0.0

103.

190.

0107

0177

36.0

8.52

9.5

55.

620.

200.

186,

970

24

2 5

9.5

29.

1<0

.10.

12<0

.010

0.05

0.06

0703

6816

.95.

6816

.02.

461.

351.

35,

540

1,83

0 1

7.8

21.

20.

20.

05<0

.010

0.12

0.02

1502

0724

.05.

8142

.25.

820.

720.

704,

400

9

2.6

7

.3 2

7.2

0.3

0.15

<0.0

10<0

.05

<0.0

123

0195

10.8

2.78

22.9

1.68

0.79

0.87

3,57

0

181

45.

1 4

1.6

<0.1

nd<0

.010

0.05

<0.0

1

2912

648.

472.

9515

.73.

160.

270.

31

34

7

0.3

24.

4 2

5.5

<0.1

nd<0

.010

2.79

<0.0

101

0039

5.40

1.84

20.5

3.01

0.15

0.16

7

2

20.

1 1

1.6

3

.42

0.2

0.02

<0.0

10<0

.05

0.29

0106

006.

821.

3819

.92.

760.

140.

15

53

9.3

10.

3

3.8

70.

10.

03<0

.010

<0.0

50.

2909

0136

9.52

1.75

31.4

3.16

0.17

0.17

10

7

<4

10.

1

9.6

40.

20.

04<0

.010

<0.0

50.

2615

0276

9.32

2.27

67.3

5.33

0.34

0.32

10

6

6

.3 1

5.6

27.

91.

40.

11<0

.010

<0.0

50.

17


Appendix � Constituent concentrations in, and characteristics of, water samples from 20 community water-supply wells, New Jersey 1998-99.—Continued

USGS well

number

1,1,1-Tri-chloro-ethane (µg/L)

(��0�)

Trichloro-ethylene

(µg/L) (�9180)

Trichloro-fluoro-

methane (µg/L)

(��88)

Vinyl chloride

(µg/L) (�91��)

m, p-Xy-lene

(µg/L) (8��9�)

o-Xylene (µg/L)

(��1��)

Xylene (µg/L)

(81��1)

030301 0.82 1.32 <0.09 <0.1 <0.06 <0.04 nd030460 0.59 0.62 <0.09 <0.1 <0.06 <0.04 nd130098 0.17 4.38 E0.09 <0.1 <0.06 <0.04 nd210402 <0.03 <0.04 <0.09 <0.1 <0.06 <0.06 nd350083 0.17 2.01 E0.04 <0.1 <0.06 <0.04 nd

270080 1.03 3.27 0.13 <0.1 <0.06 <0.04 nd270147 2.23 12.1 <0.09 <0.1 <0.06 <0.04 nd270155 0.25 <0.04 0.18 <0.1 <0.06 <0.04 nd270182 0.40 0.15 E0.03 <0.1 <0.06 <0.04 nd390451 E0.09 E0.01 <0.09 <0.1 <0.06 <0.04 nd

050039 <0.2 0.6 <0.2 <0.2 nd nd <0.2070177 <0.2 43.0 <0.2 <0.2 nd nd <0.2070368 <0.2 <0.2 <0.2 <0.2 nd nd <0.2150207 <0.2 <0.2 <0.2 <0.2 nd nd <0.2230195 <0.2 <0.2 <0.2 <0.2 nd nd <0.2

291264 0.2 0.9 <0.2 <0.2 nd nd <0.2010039 <0.2 <0.2 <0.2 <0.2 nd nd <0.2010600 <0.2 <0.2 <0.2 <0.2 nd nd <0.2090136 <0.2 <0.2 <0.2 <0.2 nd nd <0.2150276 <0.2 <0.2 <0.2 <0.2 nd nd <0.2

Appendixes �1

App

endi

x �

Conc

entra

tions

of d

isin

fect

ion

by-p

rodu

cts

form

ed in

chl

orin

ated

wat

er fr

om s

even

sel

ecte

d co

mm

unity

wat

er-s

uppl

y w

ells

in N

ew J

erse

y, 1

998-

99, d

urin

g th

ree

perio

ds o

f inc

ubat

ion.

[BR

, bed

rock

; GL,

gla

cial

; CP,

unc

onfin

ed C

oast

al P

lain

; CC

P, c

onfin

ed C

oast

al P

lain

; mg/

L, m

illig

ram

s per

lite

r; µg

/L, m

icro

gram

s per

lite

r; nd

, no

data

; <, l

ess t

han;

CH

BrC

l 2 bro

mod

ichl

orom

etha

ne; C

HB

r 3, br

omof

orm

; CH

Cl 3,

chlo

rofo

rm; C

HB

r 2Cl,

dibr

omoc

hlor

omet

hane

; B

rClA

A, b

rom

ochl

oroa

cetic

aci

d; B

r 2AA

, dib

rom

oace

tic a

cid;

Cl 2A

A d

ichl

oroa

cetic

aci

d; C

lAA

, mon

ochl

oroa

cetic

aci

d; C

l 3AA

, tric

hlor

o-ac

etic

aci

d; B

rClA

N, b

rom

ochl

oroa

ceto

nitri

le; B

r 2AN

, dib

rom

oace

toni

trile

; Cl 2A

N, d

ichl

oroa

ceto

nitri

le; C

l 3AN

, tric

hlor

oace

toni

trile

. Num

ber i

n pa

rent

hese

s is p

aram

eter

cod

e us

ed to

iden

tify

the

cons

titue

nt,

prop

erty

, or c

hara

cter

istic

in th

e U

.S. G

eolo

gica

l Sur

vey

Nat

iona

l Wat

er In

form

atio

n Sy

stem

(NW

IS) d

atab

ase.

]

USG

S w

ell

num

ber

Aqu

ifer

type

Incu

batio

n (h

ours

)

Chlo

rine

do

se

(mg/

L)

(99�

00)

Chlo

rine

re

sidu

al

(mg/

L)

(99�

01)

CHB

rCl �

(µg/

L)

(99�

0�)

CHB

r � (µ

g/L)

(9

9�0�

)

CHCl

� (µ

g/L)

(9

9�0�

)

CHB

r �Cl

(µg/

L)

(99�

0�)

BrC

lAA

(µ

g/L)

(9

9��

)

Br �A

A

(µg/

L)

(99�

1�)

Cl�A

A

(µg/

L)

(99�

09)

ClA

A

(µg/

L)

(99�

08)

Cl�A

A

(µg/

L)

(99�

10)

BrC

lAN

(µ

g/L)

(9

9�1�

)

Br �A

N

(µ

g/L)

(9

9�1�

)

2104

02B

R6

5.0

4.0

1.7

0.6

1.5

2.3

<0.1

<0.1

1.2

3.6

1.5

0.7

0.9

2104

02B

R24

5.0

4.0

3.6

0.8

2.6

3.4

1.2

1.1

1.4

<0.1

1.5

1.0

0.9

2104

02B

R16

85.

05.

06.

73.

74.

96.

33.

23.

73.

23.

81.

70.

61.

035

0083

BR

65.

04.

00.

70.

31.

20.

9<0

.1<0

.11.

2<0

.11.

2<0

.1<0

.135

0083

BR

245.

04.

01.

30.

51.

51.

5<0

.1<0

.11.

1<0

.11.

60.

5<0

.135

0083

BR

168

7.5

5.6

3.2

0.6

3.1

2.5

<0.1

<0.1

2.0

<0.1

2.6

0.6

<0.1

2701

55G

L6

5.0

4.0

1.3

0.3

4.3

1.5

<0.1

<0.1

1.6

2.0

1.6

<0.1

<0.1

2701

55G

L24

5.0

4.0

2.9

0.5

5.7

2.3

<0.1

<0.1

1.0

<0.1

1.3

0.7

<0.1

2701

55G

L16

85.

04.

05.

82.

57.

55.

42.

32.

52.

12.

81.

70.

60.

939

0451

GL

65.

04.

01.

50.

21.

71.

2<0

.1<0

.1<0

.1<0

.11.

30.

70.

739

0451

GL

247.

54.

52.

80.

33.

31.

71.

2<0

.11.

1<0

.11.

80.

90.

939

0451

GL

168

5.0

4.0

9.4

1.8

6.5

8.2

2.3

1.5

2.4

<0.1

1.8

1.5

1.5

2301

95C

P6

10.0

1.0

6.5

0.7

11.0

4.6

2.9

1.8

6.2

<0.1

6.5

2.0

1.9

2301

95C

P24

10.0

1.0

17.0

1.4

21.0

10.0

5.6

3.3

11.0

3.5

12.0

2.8

2.9

2301

95C

P16

81.

00.

529

.02.

235

.017

.08.

54.

115

.02.

313

.03.

03.

115

0207

CP

610

.02.

18.

41.

77.

57.

53.

12.

63.

3<0

.14.

03.

03.

215

0207

CP

2410

.01.

616

.02.

615

.012

.04.

02.

93.

8<0

.14.

73.

94.

715

0207

CP

168

7.5

3.4

40.0

5.9

32.0

30.0

9.3

6.1

9.6

<0.1

6.9

3.7

5.0

0106

00C

CP

6

nd

n

d4.

60.

113

.01.

91.

6<0

.14.

9<0

.12.

71.

00.

601

0600

CC

P24

n

d

nd

6.7

0.2

20.0

2.8

2.4

<0.1

6.4

<0.1

3.3

<0.1

<0.1

0106

00C

CP

168

n

d

nd

8.8

<0.1

30.0

2.3

2.5

<0.1

9.8

<0.1

4.0

<0.1

<0.1


Appendix � Concentrations of disinfection by-products formed in chlorinated water from seven selected community water-supply wells in New Jersey, 1998-99, during three periods of incubation.—Continued

USGS well

number

Aquifer type

Incubation (hours)

CL�AN (µg/L)

(99�1�)

CL�AN (µg/L)

(99�1�)

210402 BR 6 <0.1 <0.1210402 BR 24 0.6 <0.1210402 BR 168 <0.1 <0.1350083 BR 6 <0.1 <0.1350083 BR 24 <0.1 <0.1350083 BR 168 <0.1 <0.1

270155 GL 6 <0.1 <0.1270155 GL 24 <0.1 <0.1270155 GL 168 <0.1 <0.1390451 GL 6 <0.1 <0.1390451 GL 24 <0.1 <0.1390451 GL 168 <0.1 <0.1

230195 CP 6 1.8 <0.1230195 CP 24 2.1 <0.1230195 CP 168 2.0 <0.1150207 CP 6 1.4 <0.1150207 CP 24 2.0 <0.1150207 CP 168 1.2 <0.1

010600 CCP 6 1.0 <0.1010600 CCP 24 <0.1 <0.1010600 CCP 168 <0.1 <0.1

Appendixes ��

For additional information, write to:DirectorU.S. Geological SurveyNew Jersey Water Science CenterMountain View Office Park810 Bear Tavern Rd., Suite 206West Trenton, NJ 08628

or visit our Web site at:http://nj.usgs.gov/

Hopple, Jessica A., Barringer, Julia L. and Koleis, Janece—W

ater-Quality Constituents, D

issolved-Organic-Carbon Fractions, and D

isinfection By-Product

Formation in W

ater from Com

munity W

ater-Supply Wells in N

ew Jersey, 1998-99—


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