Water-Quality Constituents, Dissolved-Organic-Carbon

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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

Scientific Investigations Report 2006-5260

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

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

Scientific Investigations Report 2006-5260

U.S. Department of the Interior U.S. Geological Survey U.S. Department of the Interior DIRK KEMPTHORNE, Secretary U.S. Geological Survey Mark 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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Contents

Abstract...... 1 Introduction...... 2 Background...... 2 Purpose and Scope...... 2 Description of Study Area...... 2 Water Use and Land Use...... 4 Previous Investigations of Ground-Water Quality in New Jersey...... 4 Sources of Water-Quality Constituents and Characteristics...... 4 Volatile Organic Compounds...... 6 Nutrients...... 6 Major and Minor Ions, Trace Elements, and pH...... 7 Organic Carbon...... 7 Methods of Investigation...... 8 Well Selection...... 8 Collection and Processing of Samples...... 8 Analysis of Samples...... 8 Water-Quality Constituents...... 8 Organic Carbon Fractionation...... 9 Disinfection By-Product Formation...... 10 Carbon Fraction Preparation for Determination of Disinfection By-Product Formation...... 10 Ultraviolet Absorbance Measurements...... 11 Quality Assurance Program...... 13 Quality of Source Water to Community Water-Supply Wells...... 15 Volatile Organic Compounds...... 15 Nutrients...... 17 Major and Minor Ions, Trace Elements, and pH...... 18 Organic Carbon...... 20 Dissolved Organic Carbon Fractions and Disinfection By-Products...... 20 Organic Carbon Fractions...... 20 Disinfection By-Products...... 21 Sources...... 21 Formation of Disinfection By-Products During the Laboratory Incubation Study...... 21 Formation of Disinfection By-Products in Dissolved-Organic-Carbon Fractions...... 24 Laboratory 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...... 29 Relations Among Disinfection By-Product Formation Potentials...... 30 Origins of Selected Chemical Characteristics and Constituents and Their Effects on Disinfection By-Product Formation Potential...... 31 iv

Dissolved Organic Carbon...... 31 Bromide...... 34 Iron, Manganese, and Ammonia...... 34 Indicators of Disinfection By-Product Formation Potential...... 36 Summary and Conclusions...... 36 Acknowledgments...... 37 References Cited...... 37 Appendix 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

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 vi

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 vii

Conversion Factors and Datum

Multiply 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).

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

Abstract 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 Water samples were collected from 20 community water- (DBPs). Concentrations of the DBPs—trihalomethanes, halo- supply wells in New Jersey to assess the chemical quality of acetic acids, haloacetonitriles, and chlorate—were measured. the water before and after chlorination, to characterize the Concentrations of these compounds, with few exceptions, types of organic carbon present, and to determine the disinfec- were higher in water from Coastal Plain wells than from wells tion by-product formation potential. Water from the selected in glacial and bedrock aquifers. wells previously had been shown to contain concentrations The organic-carbon fractions were dosed with sodium of dissolved organic carbon (DOC) that were greater than 0.2 hypochlorite, incubated for 168 hours at 25 ºC, and analyzed mg/L. Of the selected wells, five are completed in unconfined for trihalomethanes, haloacetic acids, haloacetonitriles, and (or semi-confined) glacial-sediment aquifers of the Piedmont chlorate. Concentrations of trihalomethanes and haloacetic and Highlands (New England) Physiographic Provinces, five acids were higher in most of the hydrophobic organic-acid are completed in unconfined bedrock aquifers of the Piedmont fractions than in the hydrophilic fractions, with the highest Physiographic Province, and ten are completed in unconsoli- concentrations in samples from Coastal Plain aquifers. Traces dated sediments of the Coastal Plain Physiographic Province. of haloacetonitriles were measured, mostly in the hydrophilic Four of the ten wells in the Coastal Plain are completed in fraction. confined parts of the aquifers; the other six are in unconfined The aromaticity of the precursor DOC, as estimated aquifers. by measurements of the absorbance of ultraviolet light at One or more volatile organic compounds (VOCs) were 254 nanometers, apparently is a factor in the DBP forma- detected in untreated water from all of the 16 wells in uncon- tion potentials determined, as aromaticity was greater in the fined aquifers, some at concentrations greater than maximum samples that developed high concentrations of DBPs. VOCs contaminant levels. Those compounds detected included may have contributed to the organic carbon present in some aliphatic compounds such as trichloroethylene and 1,1,1-tri- of the samples, but much of the DOC present in water from chloroethane, aromatic compounds such as benzene, the triha- the 20 wells appeared to be natural in origin. The sediments lomethane compound, chloroform, and the gasoline additive of the Coastal Plain aquifers, in particular, contain substantial methyl tert-butyl ether (MTBE). amounts of organic matter, which contribute ammonia, organic Concentrations of sodium and chloride in water from one nitrogen, and aromatic DOC compounds to the ground water. well in a bedrock aquifer and sulfate in water from another Thus, the geologic characteristics of the aquifers appear to be exceeded New Jersey secondary standards for drinking a major factor in the potential for ground water to form DBPs water. The source of the sulfate was geologic materials, but when chlorinated. 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 fractions from hydrophilic fractions. Concentrations of hydrophobic acids were slightly lower than those of combined hydrophilic acids, neutral compounds, and low molecular weight compounds in most samples. Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Introduction 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 Background goal; µg/L, micrograms per liter; mg/L, milligrams per liter]

The chemical quality of a ground-water source is a Constituent/Constituent group Concentration primary concern when that source is used for public and Disinfection by-products MCL domestic supply. Regulations enacted by the U.S. Environ- mental Protection Agency (USEPA) (U.S. Environmental Trihalomethanes 80 µg/L Protection Agency, 1994) and the New Jersey Department Haloacetic acids 60 µg/L of Environmental Protection (NJDEP) (New Jersey Depart- Bromate 10 µg/L ment of Environmental Protection, 1997) require community Chlorite 1.0 µg/L water-supply purveyors to monitor ground water for a variety Residual disinfectant MRLG of contaminants that include radionuclides, trace elements, Chlorine 4 mg/L and volatile organic compounds (VOCs) (for example, Louis Chloramines 4 mg/L and others, 1994). The U.S. Geological Survey (USGS), in Chlorine dioxide 0.8 mg/L cooperation with NJDEP, has participated in several research 1 U.S. Environmental Protection Agency, 1994 projects investigating the relation of the chemical quality of water to hydrogeology and to land use. These studies have the quality of source water to 20 community supply wells and been designed to assess the vulnerability of the source waters to investigate a method for predicting the formation of DBPs. of community water-supply wells to contamination by pesticides, radionuclides, VOCs, and compounds that form as a result of disinfection of drinking water, known as disinfection Purpose and Scope by-products (DBPs). This report describes a study to determine (1) whether the The results of the vulnerability studies can be used by quality of source water to 20 community water-supply wells water-supply managers to evaluate strategies for monitoring across New Jersey was compromised by contaminants, and (2) the quality of water in community water-supply wells. Moni- whether the vulnerability of water from community water- toring requirements for certain constituents could be waived or supply wells to contamination by the formation of DBPs can reduced for wells that are not vulnerable to human or natural be predicted on the basis of hydrogeologic and water-quality sources of contamination. indicators. The quality of water withdrawn from the supply New regulations adopted by USEPA, with respect to wells was determined and is assessed in light of contaminant the Disinfection By-Products Rule (DBPR) and the Infor- inputs to ground water from natural sources and human activ- mation Collection Rule (ICR), increased the requirements ity. As possible precursors to DBP formation, various types of for water purveyors to collect detailed information on both organic carbon are identified and their relation to the potential source waters and treated waters. The DBPR, which sets for DBP formation in water from confined and unconfined maximum contaminant levels (MCLs) for trihalomethanes aquifers is evaluated. Water-quality and quality-assurance data (THMs), haloacetic acids (HAAs), bromate, and chlorite, and are presented and discussed. maximum residual disinfection concentrations for chlorine, chloramines, and chlorine dioxide (table 1), was established in 1994 (U.S. Environmental Protection Agency, 1994). Stage 1 Description of Study Area 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 New Jersey has a humid, temperate climate; average HAAs at 60 µg/L was established. annual precipitation is about 45 inches. The State contains The ICR requires utilities that get their water from parts of four major physiographic regions or provinces known ground-water sources and that serve populations greater as the Coastal Plain, the Piedmont, the Highlands (otherwise than 50,000 to start monitoring for DBPs and microbial known as the New England Province), and the Valley and contaminants. A method is needed to determine whether the Ridge provinces (fig. 1). Within these provinces, different vulnerability of water from community water-supply wells geologic settings create a variety of aquifer types. to contamination from DBPs can be predicted on the basis of Aquifers consisting of unconsolidated sediments underlie source-water chemical constituents derived from human or most of the Coastal Plain Physiographic Province in southern natural inputs. This method could be used by water mangers New Jersey and are present in glacial deposits in northern to assess the need for chemical analyses of water supplies New Jersey. The aquifers of the Coastal Plain vary in areal that may be of low vulnerability. This vulnerability study was extent and thickness and consist of permeable units of sand conducted by USGS, in cooperation with NJDEP, to determine and gravel that are separated from one another by less permeable confining units of silt and clay. Sediments of the predomi- Introduction

75 74

41 030301 270080 VALLEY AND RIDGE 030460 270182 270155 270147 130098

NEW ENGLAND (HIGHLANDS) 390451 350083 PIEDMONT EXPLANATION 230195 WELL LOCATION AND NUMBER-- 291264 210402 Color identifies type of aquifer:

Glacial

Coastal Plain, unconfined

Coastal Plain, confined 291264 050039 Bedrock 40 070368 070177

150207

150276 COASTAL PLAIN

010039 010600

090136 0 10 20 MILES

0 15 30 KILOMETERS 39

Figure 1. Physiographic provinces of New Jersey and locations of community water-supply wells sampled during 1998-99. Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 nantly unconfined Kirkwood-Cohansey aquifer system crop Previous Investigations of Ground-Water Quality out over 3,000 mi2 of the Coastal Plain. The aquifer system in New Jersey is confined on the Cape May peninsula at the southern tip of the State and near the Atlantic coastline (Zapecza, 1989). Five A summary of the quality of New Jersey ground water other major aquifers or aquifer systems composed of uncon- and a discussion of the vulnerability of water supplies to solidated sediments underlie the Kirkwood-Cohansey aquifer contamination is presented in Ayers and Pustay (1988) as system; these are mostly confined except in areas along the part of the U.S. Geological Survey National Water Summary. western and northern parts of the Coastal Plain, where their Pesticides and nutrients were measured in water from 90 com- sediments are at land surface (fig. 2). The glacial aquifers munity water-supply wells during 1994-95 (Clawges and oth- typically are composed of valley-fill sediments, are mostly ers, 1998). The occurrence of nitrates, pesticides, and VOCs unconfined, and generally are present north of the terminal in ground water in southern New Jersey was determined by moraine of the last (Wisconsin) period of glaciation. Bedrock Stackelberg and others (1997). THM formation potential, how- aquifers, which are mostly unconfined, occur in fractured ever, has not been studied previously in New Jersey ground shales and sandstones in the Piedmont Province, in weathered waters, but an investigation of the formation potential in water and fractured crystalline rocks of the Highlands Province, and in Kansas aquifers has been reported by Miller and others in porous limestones and dolomites, and fractured conglomer- (1990). ates, sandstones, siltstones, and shales of the Valley and Ridge Province. Sources of Water-Quality Constituents Water Use and Land Use and Characteristics Freshwater use in New Jersey, the most populous of the 50 United States, currently is estimated at about 2,200 mil- The concentrations of chemical constituents in ground lion gallons per day. About 27 percent of this volume comes water are related to the sources of the constituents and to from ground water, of which about 67 percent is provided by the physical, biological, and chemical processes that have community water-supply wells (John Nawyn, U.S. Geological occurred along ground-water flow paths. Some sources of con- Survey, written commun., 2003). stituents occur naturally; others result from human activities. The quality of the water provided by wells completed Natural sources of constituents include those in precipitation in unconfined aquifers can be affected by contaminants entering aquifers as recharge, minerals and organic matter in introduced at or near the land surface by human activities. soils, and the minerals and organic matter that compose the Confined aquifers, which can contain water that entered as aquifer matrix. In some hydrogeologic settings, surface water recharge hundreds to thousands of years ago, are less vulner- also can provide recharge and can contribute constituents to able to this type of contamination. Water in both aquifer types, ground water. Human-induced sources from the land surface however, can be affected by naturally occurring contaminants and subsurface include applications of agricultural chemi- released by the aquifer materials. cals, and disposal of industrial chemicals and other wastes. Agricultural, residential, and urban developments consti- Natural processes affect the concentrations of both natural tute the predominant uses of land in New Jersey. A substantial and human-induced constituents—these processes include increase in residential development since World War II has biological degradation of organic matter, mineral dissolution occurred largely, although not entirely, at the expense of agri- and precipitation, ion exchange, oxidation-reduction reactions, cultural land. Land development brings with it the potential adsorption and desorption of solutes, and generation/coagula- for contamination of ground water. Agricultural practices can tion of colloids. contribute contaminants through use of fertilizers and pesti- Because certain constituents in drinking water are known cides; residential, commercial, and industrial activities can to pose human health hazards, standards have been set for contribute contaminants through the use of septic tanks and these constituents by the USEPA and by State agencies such releases of fuels, solvents, and other chemicals. Large tracts of as NJDEP (U.S. Environmental Protection Agency, 2001; undeveloped land remain, primarily in southern New Jersey. New Jersey Department of Environmental Protection, 1997). Ground-water quality is less likely to be adversely affected in The National Primary Drinking Water Regulations set either these areas than in developed parts of the State, unless ground- a maximum contaminant level (MCL), which is the maxi- water flow moves contaminants from parts of the aquifers mum permissible level of a contaminant in water delivered to underlying developed land to those parts underlying adjacent a public system, or an Action Level (AL), the concentration undeveloped areas. 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, Sources of Water-Quality Constituents and Characteristics

EXPLANATION

GEOLOGIC UNITS 75 Glacial sediment 74 Holocene age sediments of the Coastal Plain

Kirkwood and Cohansey Formations 41 030301

Mt. Laurel and Wenonah Formations 270080 030460

Potomac, Raritan, and Magothy Formations 270182 270155 Other unconsolidated sedimentary Formations 270147 130098 Stockton Formation 390451 Passaic Formation

Boonton Formation 350083 Other bedrock Formations

Crystalline Rocks 230195

Extent of Terminal Moraine 210402

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

Glacial

Coastal Plain, unconfined 050039 291264

Coastal Plain, confined 40 Bedrock 070368 070177 150207

150276

010039 010600

0 10 20 MILES 090136

0 15 30 KILOMETERS

Figure 2. Geologic and hydrogeologic features of New Jersey. Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 more stringent than the Federal standards and include second- men and Burn, 1993; Smith and others, 1988; Verschueren, ary maximum contaminant levels (SMCLs), which are not 1983). based on health issues, but on the aesthetic issues of smell, Some VOCs occur naturally; the ethylene emitted as gas taste, foaming, staining, and corrosiveness to plumbing. The by ripening fruit is an example. Of the trihalomethanes, chlo- NJDEP drinking-water standards for the constituents analyzed roform has been shown to form naturally (Hoekstra and others during this investigation are listed in table 2. 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) Volatile Organic Compounds disposal at the land surface or in the subsurface can lead to contamination of underlying aquifer systems, and, in some VOCs are a class of organic compounds, primarily instances, to contamination of water tapped by community halogenated aliphatic and monocyclic aromatic hydrocarbons, water-supply wells. that are characterized by high vapor pressures; that is, they Many VOCs are toxic and (or) carcinogenic; conse- volatilize easily, and they are highly soluble (Smith and others, quently, MCLs have been developed for these compounds. 1988). MCLs range from 1 to 1,000 µg/L, depending on the toxicity VOCs have a multitude of uses in modern society. VOCs of the compound (table 2) (New Jersey Department of Envi- are present in fuels and the exhaust from their combustion. ronmental Protection, 1997). 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 Nutrients are widely used in industrial applications as degreasers and refrigerants, in the dry-cleaning industry, in the manufacture Nutrients, which include nitrogen and phosphorus and of pharmaceutical products and plastics, in a process used to their compounds, are essential for animal and plant growth. decaffeinate coffee, and in agricultural applications as active Natural sources of nutrients include wet and dry atmospheric and inactive components of pesticides and fumigants (Bloe- deposition, biologically-mediated fixation, and the dissolution

Table 2. 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 1 Carbon 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 4 1,2-Dichloroethane 2 Nitrate [as nitrogen] 10 1,1-Dichloroethylene 2 Nitrite [as nitrogen] 1 cis-1,2-Dichloroethylene 70 Characteristics SMCL trans-1,2-Dichloroethylene 100 pH 6.5-8.5 optimum 1,2-Dichloropropane 5 Inorganic Constituents SMCL (mg/L) Ethylbenzene 700 Chloride 250 Methyl tert-Butyl Ether 70 Fluoride 2 2 Methylene Chloride 3 Hardness [as CaCO3] 250 (Mono) Chlorobenzene 50 Iron 0.3 Styrene 100 Manganese 0.05 Tetrachloroethylene 1 Sodium 50 Toluene 1,000 Sulfate 250 1,1,1-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) Sources of Water-Quality Constituents and Characteristics or precipitation of organic matter. Anthropogenic point sources such as iron and manganese) are contributed to ground water of nitrogen and phosphorus, as elements or compounds, mainly through weathering processes that result in dissolu- include municipal and industrial discharges and effluent tion of minerals in soils, sediments, and bedrock. Major ions from individual septic systems or cess pools. Anthropogenic such as calcium, magnesium, potassium, chloride, and sulfate nonpoint sources include leaching of domestic and agricultural also can be contributed to ground water by land application fertilizers, manure deposited on or applied to the land sur- of agricultural chemicals. Wastewater discharges contribute face, and effluent from leaking sewer lines or groups of septic major ions, particularly sodium, chloride, bicarbonate, and systems. sulfate, and trace elements. In some areas, use of road salt Ammonia is generally the predominant form of nitro- during winter can lead to increases in sodium and chloride in gen in agricultural fertilizers and septic-system effluents. ground water. Ammonia (or ammonium ion) is volatile and, therefore, can There also are inputs to the land surface from atmo- be transported through the atmosphere and deposited in wet or spheric deposition, both wet (precipitation) and dry deposi- dry form. In the presence of oxygen it is converted to nitrite, tion. Mineral sources of chloride, for example, generally are then to nitrate through a microbiologically mediated process not abundant, but precipitation can be an important source of called nitrification. The ammonium ion also adsorbs to miner- this ion; concentrations of sodium and calcium also tend to be als (Hem, 1992), and thus is retarded as it moves through soils high in precipitation in New Jersey (Graedel and Reiss, 1985). and aquifer materials. Consequently, because of oxidation Because chloride tends not to adsorb to soil materials, it can (nitrification) and (or) retardation through adsorption, concen- move easily from the land surface to the water table. trations of ammonia in ground water are usually low, unless Bromide and fluoride typically are present in minor the geochemical environment of the aquifer is reducing (little amounts in ground water. Bromide is contributed primarily or no oxygen). Furthermore, because nitrite quickly oxidizes by precipitation and can be of natural origin (for example, salt to nitrate, nitrite also generally remains at low concentrations spray, which also contributes chloride) or from anthropogenic in both surface and ground water. Nitrate is present in some sources. Fluoride typically is derived from dissolution of min- fertilizers and enters the atmosphere from auto exhaust and erals in the aquifer matrix (Hem, 1992). industrial smokestacks. Consequently, infiltration of precipita- Most of the trace elements in ground water are metal tion can be a source of ammonia, nitrite, and nitrate ions to and metalloid ions such as aluminum, arsenic, copper, lead, ground water. Nitrate from fertilizer, and animal (and human) iron, and manganese. Minerals in the aquifer matrix typically wastes leaches easily through soils (Hem, 1992); as a result, contribute metals such as aluminum, iron, and manganese; concentrations in ground water can exceed 10 mg/L, particu- other metals and metalloids also can be derived from mineral larly in agricultural areas. In reducing parts of an aquifer, sources. Industrial releases to the land surface and subsurface, however, nitrate may not be detected, whereas ammonia (and also pesticide use, can contribute metallic and metalloid trace perhaps nitrite) are likely to be detected. elements, sometimes at high concentrations, to ground water An MCL (10 mg/L as N) has been promulgated for nitrate (Hem, 1992). Metals emitted by industrial activities also are in drinking water because high concentrations can cause the deposited from the atmosphere to the land surface. Manga- potentially fatal blood disorder called methemoglobinemia, nese, for example, is present mostly in particulate form, and or “blue baby disease;” this primarily affects children under is deposited near its sources (Adriano, 1986). Acidic precipi- 6 months of age. High concentrations of nitrite can cause the tation can leach metals from soils, but some, such as lead, same disorder. As a result, an MCL (1 mg/L as N) has been with an affinity for soil organic matter and clays, tend to be developed for nitrite as well (table 2). No MCL for ammonia adsorbed (Adriano, 1986) and thus retained in the soils. has been developed. Ground-water pH (hydrogen-ion activity) is controlled Phosphorus is an essential element in metabolism. by a variety of chemical reactions that consume or produce Organic phosphorus species synthesized by plants and animals hydrogen ions. These reactions include dissociation of water, constitute a significant fraction of phosphorus in many natural interactions between water and gases, dissolution of miner- waters (Hem, 1992), where it is usually found in concentra- als, hydrolysis of metal ions, and oxidation/reduction (redox) tions less than a few tenths of a part per million. Large quanti- reactions (Hem, 1992). These reactions take place in the soil, ties of phosphorus are introduced to the environment through between recharge waters and soil constituents, and in the aqui- the use of fertilizers; because phosphorus binds strongly fer, between water and aquifer materials. Insofar as chemicals to fine-grained soils and organic material, phosphate from of anthropogenic origin can be involved in some of these reac- fertilizer or organic wastes typically does not leach easily into tions, the pH of ground water, on a local scale, can be affected ground water. by human activities.

Major and Minor Ions, Trace Elements, and pH Organic Carbon

Major ions (calcium, magnesium, sodium, potassium, Natural sources of organic carbon in ground water chloride, and sulfate) and trace elements (arsenic and metals include (1) decomposing plants and other organic matter that 8 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 infiltrate in recharge from soils, or are carried in recharge samples were collected at the wellhead prior to any disinfec- by surface waters to ground water, and (2) altered (in some tion or other treatment to represent the quality of the water cases, fossilized) remnants of organic matter, such as lignite from the aquifer before treatment. Flow from the wellhead and kerogen, in the geologic materials that compose aquifers was routed through Teflon tubing into an instrumented (Thurman, 1985). Anthropogenic sources of organic carbon flow-through cell in which water temperature, pH, specific include septic-system effluent, animal feedlots, and compost- conductance, and dissolved oxygen (DO) were measured ing facilities. Decomposing VOCs also can contribute organic continuously. These measurements were recorded every 3 to carbon to ground water. 5 minutes until differences in values for three or more succes- Organic carbon can be measured as total organic car- sive measurements fell within the following criteria: tempera- bon (TOC), which includes particulate and dissolved organic ture, 0.2 ºC; 0.05 pH units; 5 percent of specific conductance carbon (DOC), which is defined as the organic carbon that values less than or equal to 100 µS/cm (microsiemens per passes through a 0.45 µm pore-size silver or 0.7 µm pore-size centimeter) or 3 percent of specific conductance values greater glass-fiber filter. DOC has been considered the chemically than 100 µS/cm; and DO, 0.3 mg/L. This approach ensured the reactive fraction and is composed mostly of humic substances collection of fresh water from the aquifer rather than stand- and hydrophilic acids (Thurman, 1985). Nevertheless, because ing water from the well casing. Upon stabilization of the field colloids are increasingly found to be involved in contami- measurements, the sample flow was routed into a polyethylene nant transport in aquifers, organic carbon (humic substances, sample-collection chamber in order to minimize exposure to lignin) as colloids or as coatings on inorganic colloids can air-borne contaminants. play a role in both soil and ground-water contaminant mobility Samples for VOC analysis were collected by filling the (McCarthy and Zachara, 1989; Kretzschmar and others, 1995). sample vial from the bottom with a Teflon tube and allowing Consequently, determinations of TOC can be useful to the the vial to overflow before capping. Samples collected for understanding of transport of adsorbed constituents in ground analysis for total organic carbon (TOC), DOC, and ultraviolet water. 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- Methods of Investigation 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 Well Selection liter (L) of native water prior to sample collection. Samples for analysis of major cations and trace elements were preserved Wells to be sampled were selected on the basis of previ- with nitric acid according to USGS protocols. Alkalinity was ous water-quality results reported in the USGS National Water measured in the field by incremental titration (Koterba and Information System database. An emphasis was placed on others, 1995). wells completed in unconfined aquifers because the vulner- In addition to the samples of untreated water for analysis ability of those wells to human-induced contaminants was of water-quality constituents, three 1-L water samples were considered high relative to that of wells completed in confined collected from each well for determination of DBP formation aquifers or in confined parts of aquifers. Existing water-qual- potential. Additional 1-L samples were collected from selected ity data for the chosen wells indicated that those in the Coastal wells for determination of the rate of DBP formation. All Plain generally yielded water containing higher concentrations samples for laboratory analysis were chilled on ice immedi- of DOC, and thus, the water could have a higher potential ately following collection and were shipped overnight to the for forming DBPs than water from the other physiographic analyzing laboratories. provinces. Wells yielding water with low DOC concentrations (less than 0.2 mg/L) were not chosen for sampling because Analysis of Samples 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. Water-Quality Constituents The water samples were analyzed at four laboratories Collection and Processing of Samples (table 4). Samples for major ions, trace elements, nutrients, and VOCs were analyzed at the USGS National Water Qual- Water samples were collected from the 20 selected wells ity Laboratory (NWQL) in Arvada, Colorado. Samples were during 1998–99. Sampler tubing and connectors were cleaned analyzed for DOC and TOC at NWQL and the USGS National following procedures described by Koterba and others (1995); Research laboratory, Boulder Colorado. Methods used are DOC filter units were cleaned in a sonifier using three suc- described by Connor and others (1998); Brenton and Arnett cessive rinses of organic-free de-ionized water. Ground-water (1993); and Fishman and Friedman (1989). Measurements of Methods of Investigation 9

Table 3. 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] Land- surface Total Top of Bottom USGS Aquifer elevation well open of open well Aquifer name Geologic description of aquifer materials type (ft above depth interval interval number NGVD (ft BLS) (ft BLS) (ft BLS) 1929) 030301 Brunswick BR Red shale, some black shale 220 256 nd nd 030460 Passaic BR Red shale, some black shale 32 402 46 402 130098 Passaic BR Red shale, some black shale 200 551 56 551 210402 Stockton BR Arkosic sandstone 50 302 nd nd 350083 Passaic BR Red shale, some black shale 55 400 53 400

270080 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 520 150 88 143 270147 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 190 115 85 115 270155 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 330 75 60 75 270182 Stratified Drift GL Sand/gravel, rock clasts, some carbonate 180 47 30 47 390451 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 57 070177 Lower PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 9 304 274 304 070368 Lower PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 10 138 106 126 150207 Lower PRM aquifer system CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 30 282 241 282 230195 Oldbridge (PRM) CP Quartz sand/gravel/silt/clay, mica, lignite (OM) 15 80 50 80 291264 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 10 788 733 788 010600 Atlantic City 800-foot sand CCP Quartz sand/gravel/silt/clay, mica, some OM 8 810 750 810 090136 Atlantic City 800-foot sand CCP Quartz sand/gravel/silt/clay, mica, some OM 7 834 802 834 150276 Upper PRM aquifer system CCP Quartz sand/gravel/silt/clay, mica, lignite (OM) 60 289 242 289

UV-254 were made at the National Research laboratory in 1.99. Columns containing non-ionic acrylic-ester copoly- Boulder and at the USGS New Jersey Water Science Cen- mer resins XAD-8 and XAD-4 were connected in series and ter laboratory in West Trenton, New Jersey, using Standard used to extract hydrophobic and hydrophilic carbon frac- Method 5910 (Eaton and others, 1995). Incubation studies and tions in selected samples (fig. 3). Hydrophobic organic acids DBP analysis using USEPA Standard Methods (table 4) were were extracted onto the XAD-8 resin in the first column performed at the Environmental Health Laboratory (EHL), in and retrieved by back-eluting with 0.1 N sodium hydroxide South Bend, Indiana. The minimum reporting limit (MRL), (NaOH) for all samples. The hydrophilic organic acids, which which is the minimum concentration of an analyte that can be passed through the first column, were retained on the XAD-4 reliably measured by the laboratory using a given analytical resin, and, for six samples, were retrieved by again back-elut- method, is shown for each constituent in table 5. (For VOCs, ing with NaOH. Both eluates were immediately acidified with some detections are reported as estimated concentrations HCl to a pH between 1.90 and 1.99 to prevent organic carbon below an MRL of 0.2 µg/L, however, and the actual estimated degradation (Aiken and others, 1992). The low-molecular- values do not appear in data tables in appendix 2.) weight hydrophilic (transphilic) compounds passed through both columns. Organic Carbon Fractionation Both the hydrophobic organic acids and the hydrophilic organic acids then were further concentrated on the XAD-8 Because organic acids are absorbed in the proton- and XAD-4 columns, respectively. The columns were desalted ated form (Thurman, 1985), DOC samples were acidified, with deionized water and the samples back-eluted with NaOH using hydrochloric acid (HCl), to a pH between 1.90 and onto separate cation-exchange resins to hydrogen-saturate the 10 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Table 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.

[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 Field pH Meter Field Specific conductance Meter Field Dissolved oxygen Meter Field Alkalinity Incremental titration Field Volatile organic compounds Purge and trap GC/MS NWQL Nutrients Colorimetry NWQL Major ions; trace elements Inductively coupled plasma spectroscopy NWQL Total 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 EHL Haloacetic acids USEPA Standard Method 552.21 EHL Haloacetonitriles USEPA Standard Method 551.11 EHL Chlorate USEPA Standard Method 300.01 EHL Chloral hydrate USEPA Standard Method 551.11 EHL 1 Eaton and others, 1995 samples. The desalted samples then were acidified to a pH Methods listed in table 4. The dosed samples were incubated between 1.90 and 1.99 to prevent degradation. for 168 hours (seven days) at 25 ºC; then the samples were The hydrophobic fraction was isolated from all the analyzed for residual chlorine. The sample of each set of three hydrophilic fractions in the remainder (14) of the samples, in which the concentration of residual chlorine was closest to using only the XAD-8 resin columns. For these samples, only 5 mg/L then was analyzed for chlorate (EPA Method 300.0) the fractions DOC 1 (the influent solution), DOC 2 (hydro- and four types of post-chlorination DBPs—THMs (EPA philic organic acids), DOC 3 (hydrophobic organic acids), and Method 524.2), haloacetic acids (HAAs) (EPA Method 552.2), DOC 4 (hydrophobic organic neutrals) are available (fig. 3). haloacetonitriles (HANs), and chloral hydrate (EPA Method The concentration of hydrophobic neutral compounds, which 551.1). The additional 1-L samples collected from selected are retained on the XAD-8 resin, can be calculated (table 5), wells for determination of DBP formation rate were treated as as can the hydrophilic neutral compounds (fraction DOC 7), above, but concentrations of DBP were measured after 6-hour which are retained on the XAD-4 resin columns used in most and 24-hour incubation periods. of the fractionations. These calculated concentrations should have a positive or zero value. A positive value represents the concentration of Carbon Fraction Preparation for Determination neutral compounds retained on one or the other resin columns, of Disinfection By-Product Formation whereas a zero value indicates that no neutral compounds are present. A negative value indicates that leaching of organic The 1-L samples collected for both fractionation and carbon from the resin column has occurred. Such leaching is determination of DBP formation were fractionated onto not uncommon in samples containing low (about 0.2 mg/L or 20-mL columns according to the procedure described above. less) concentrations of DOC. The full fractionation method is DOC and UV-254 were measured following each step in the summarized in table 6. 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 Disinfection By-Product Formation organic-carbon analyzer caused by the presence of HCl. Splits of the fractionated samples were sent to EHL to be Upon arrival at the analyzing laboratory, the 1-L water dosed with NaOCl, incubated, and analyzed for DBPs. The samples collected for determination of DBP formation were concentrations of NaOCl needed to obtain a residual chlorine adjusted to pH 7. The three samples from each site were concentration of 5 mg/L were estimated by laboratory person- dosed with sodium hypochlorite (NaOCl), one bottle each at nel from the amount of NaOCl with which the corresponding 5, 7.5, and 10 mg/L, respectively, following EPA Standard whole-water sample was dosed. After a 168-hour incubation Methods of Investigation 11

Table 5. 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, disinfection 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

period at 25 ºC, the fractions were analyzed for THMs, HAAs, order to avoid absorption interferences by particulate mat- HANs, and total chlorine residual. ter. Other interferences in UV absorption may arise from the presence of large concentrations of ferrous iron, nitrate, nitrite, Ultraviolet Absorbance Measurements bromide, chlorate, chlorite, and chloramines, as noted in EPA Method 415.3 (Eaton and others, 1995). Consequently, sam- Organic constituents absorb ultraviolet (UV) light in ples with high iron concentrations (> 1,000 µg/L) were filtered proportion to their concentration. Measurements of UV-254 twice to remove any iron-bearing particulates. Measurements are directly related to concentration and the aromaticity of a are made, using a spectrophotometer, by placing an aliquot of compound (Eaton and others, 1995). Specific UV absorbance, sample in a quartz glass cuvette and measuring the absorbance which is UV-254 normalized to the concentration of DOC at 254 nanometers. The absorbance value is compared with a (SUVA = UV-254/DOC x 100), relates to the aromaticity. standard curve developed by determining absorbance of solu- Water samples for UV-254 analysis typically are filtered in tions of known, standard concentration. 1 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Sample In - DOC1

XAD-8 Column

DOC4 NaOH XAD-8 Eluate - DOC3 Hydrophobic Hydrophobic organic acids neutrals sorbed onto or leached from column

XAD-8 Efﬂuent - DOC2

XAD-4 Column

DOC7 NaOH XAD-4 Eluate - DOC6 Hydrophilic Hydrophilic organic acids neutrals sorbed onto or leached from column

XAD-4 Efﬂuent - DOC5 Low molecular weight hydrophilic compounds

Figure 3. 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) Methods of Investigation 13

Table 6. 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 All measurable organic carbon in sample onto XAD-8 column) DOC 2 XAD-8 effluent - all that passes through column Hydrophilic organic acids and neutrals Low-molecular-weight hydrophilic compounds DOC 3 XAD-8 eluate - compounds initially retained Hydrophobic organic acids (humic and fulvic acids) on XAD-8 column and eluted with NaOH 5-9 carbon aliphatic acids 1 and 2 ring aromatic carboxylic acids 1 and 2 ring phenols DOC 4 DOC 1 - [DOC 2 + DOC 3] Calculated – hydrophobic organic neutrals; calculated value > 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 Hydrophilic organic acids; polyfunctional organic acids; on XAD-4 column and eluted with NaOH < 6-carbon aliphatic acids

DOC 7 DOC 2 - [DOC 5 + DOC 6] Calculated – hydrophilic organic neutrals; calculated value > 0, retained on column, < 0, leached from column

Quality Assurance Program submitted for analysis and tabulated statistics on the results are reported. A quality-assurance program was designed to evalu- Results of analysis of field-replicate samples are listed in ate the accuracy and precision of the water-quality data and appendix 1a. Differences between concentrations of replicate ensure that results are representative of actual environmental samples are within the uncertainty of the significant figures concentrations. Quality-assurance samples were collected used in reporting concentrations. Concentrations detected following procedures in Koterba and others (1995). Replicate in blank samples also are listed in appendix 1a. Summary samples (20 percent of environmental samples) were col- information is listed in table 7. Concentrations of DOC were lected in succession to determine whether sample-collection detected by the NWQL and the Boulder, Colorado, labora- techniques were reproducible, the chemical composition of the tories in the pre-sampling blank collected on July 21, 1998. water sample changed during sample collection, and analyti- Low-level organic-carbon contamination was present in cal results were reproducible. Equipment blanks (20 percent the volatile-grade blank water (K.D. Pirkey, NWQL, writ- of environmental samples) were collected prior to sampling ten commun., 1998). Silica was present in the first blank and after the final well was sampled during the two sampling because of contamination from the borosilicate glass nitric rounds to determine whether analytical results were biased by acid ampule (E.J. Zayhowski, NWQL, oral commun., 1998) interferences introduced during the process of cleaning and but no explanation can be made for the low-level detection storing sample collection equipment, or during sample collec- of ammonia. Results of the analysis of the blank collected tion, handling, preserving, or shipping procedures. Nitrogen- August 27, 1998, yielded no detectable concentrations with purged VOC-free blank water, obtained from NWQL, was the exception of DOC and TOC detections by the Boulder, used for organic blanks. Inorganic blank water, obtained from Colorado, laboratory. The low-level concentrations of silica the USGS Quality Water Service Unit Laboratory in Ocala, and ammonia detected in the first blank are not sufficiently Florida, was used for inorganic blanks. Quality-assurance great to negatively affect the environmental data. Concentra- procedures for reported data included checking the ion balance tions of DOC and TOC were consistently less in samples for each sample, comparing field and laboratory pH, specific analyzed by NWQL compared with those in samples analyzed conductance, and alkalinity values, and requesting reruns if in the Boulder, Colorado, laboratory. Because of analytical any aspects of the results were questionable. and instrument variability associated with low organic carbon The internal quality-control program followed by the concentration samples, the differences are within acceptable NWQL is documented by Friedman and Erdmann (1982) and limits. The results from the Boulder laboratory are not pre- Pritt and Raese (1995). The NWQL participates in the USGS sented in this report. Quality Assurance Program, under which standard samples are Data on DBP formation in equipment blanks also are summarized in table 7 and presented in appendix 1-2. Of the 1 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Table 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.

[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 Purpose, results, and conclusions number of samples (x) 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: Results: NWQL Organics: No VOCs detected in blank. NWQL: DOC and TOC detected at 0.2 mg/L in one sample using VOC blank water (2) 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 Results: (2) 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 Results: One UV-254 of 0.002, less than any environmental samples. Science Center Conclusions: UV-254 results were reproducible; no bias is introduced. laboratory (2) Disinfection by- Results: products: Organics: THMs and HAAs were detected in blanks; some detections may result from organic carbon contamination of blank EHL water. (2) 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: Results: NWQL, Organics and Inorganics: Replicates were within expected range of reproducibility. (2) Conclusions: Analytical results were reproducible, no bias is introduced. Boulder, Colorado Results: (2) 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 Results: Replicates were within expected range of reproducibility. Science Center Conclusions: Analytical results were reproducible; no bias is introduced. laboratory (2) Disinfection by- Results: products: Organics: High variability in concentrations of HAA in three of four replicate sets. EHL Inorganics: Replicates were within expected range of reproducibility. (2) 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. Quality of Source Water to Community Water-Supply Wells 15

THMs, chloroform was detected in all blanks at concentra- Volatile Organic Compounds tions ranging from 0.7 to 6.8 µg/L; bromodichloromethane and dibromochloromethane were detected at 0.8 and 0.1 No VOCs were detected in water from the wells in µg/L, respectively, in one blank. Eight environmental samples confined aquifers of the Coastal Plain (app. 2), an anticipated contained chloroform at a concentrations less than the high result, as the four wells are located more than 30 mi down- blank concentration. Four of the five HAAs (bromochloro- gradient from the outcrop areas of the aquifers and withdraw acetic acid, dichloroacetic acid, monochloroacetic acid, and water that is several thousands of years old. VOCs were trichloroacetic acid) were detected in from one to three of detected in water from all the wells in unconfined aquifers, the four blank samples. Some of the HAA detections in the however. Of the aromatic VOCs (those containing one or more blanks were less than the environmental samples, but many benzene rings), the most common are components of gasoline were at similar levels. Low-level organic carbon contamina- and other petroleum compounds; these often are referred to as tion of the blank water may be the cause of the detections of BTEX—for benzene, toluene, ethylbenzene, and xylenes. Ben- chloroform and HAAs in the blanks from 1998. No HANs zene was the only BTEX compound detected; it was detected were detected in the blank samples. Chlorate was detected in in water from wells in the unconfined aquifers. Benzene was the blank samples at concentrations ranging from 95 to 2,100 detected at a concentration less than the MRL in water from a µg/L. Chloral hydrate was detected in the blank samples at well (030460) completed in a bedrock aquifer and a concentra- concentrations ranging from 1.2 to 120 µg/L—the concentration of 0.5 µg/L—less than the MCL of 1 µg/L—in water from tion of 120 µg/L was reported as “high biased,” being more a well (291264) completed in a Coastal Plain aquifer. Other than an order of magnitude greater than the high concentration aromatic VOCs—1,2-dichlorobenzene, 1,3-dichlorobenzene, in the environmental samples. Because of the wide range and and 1,4-dichlorobenzene—were detected, but only in water high bias of concentrations in the blanks, interpretation of the from the Coastal Plain well (291264) in which benzene was chlorate and chloral hydrate data for environmental samples is detected (app. 2). not possible; thus, chlorate and chloral hydrate incubation data Commonly detected aliphatic compounds include chlo- for environmental samples are not reported. rinated solvents such as tetrachloroethylene (PCE), trichloroethylene (TCE), and the compound currently used to oxygen- ate gasoline— methyl tert-butyl ether (MTBE). At least one Quality of Source Water to Community aliphatic VOC was detected in water from each well in the unconfined aquifers (app. 2). The most commonly detected Water-Supply Wells aliphatic VOC was MTBE, in water from 13 of the 16 wells in unconfined aquifers (fig. 4a); none of the concentrations The water samples that were collected from the 20 com- exceeded the MCL of 70 µg/L, however. TCE, the next most munity water-supply wells are representative of the water commonly detected compound, was present in water from withdrawn from the well before treatment. The water that 11 of the 16 wells in the unconfined aquifers. Concentrations reaches the open interval of a large-volume well, such as a of TCE exceeded the MCL (1 µg/L) in water from six wells, supply well, may originate, in part or entirely, from areas ranging from 1.32 to 43 µg/L (fig. 4b). Other compounds outside the immediate area of the wellhead, depending upon with high detection frequencies in water from the wells in factors such as well depth, aquifer characteristics, location of unconfined aquifers were 1,1,1-trichloroethane (10 wells), the well in the local flow system, and stresses created on that 1,1-dichloroethane and cis-1,2-dichloroethylene (9 wells flow system by other pumped wells. Because supply wells each), and PCE (8 wells). None of the first three compounds withdraw large volumes of water, water containing contami- were present at concentrations that exceeded MCLs (30, 50, nants originating in part of the contributing area to the well 70, and 1 µg/L, respectively), but concentrations of PCE may be diluted by uncontaminated water from other parts of exceeded the MCL in water from five of the eight wells (fig. the contributing area as mixing of water takes place in the 4c). TCE and PCE exceeded MCLs in water from more wells immediate vicinity of, or within, the well bore. Consequently, in bedrock aquifers than in water from wells in either glacial concentrations of contaminants in water from supply wells or Coastal Plain aquifers. The concentration of 1,2-dichloro- may not represent the maximum concentrations in at least ethane exceeded the MCL (2µg/L) in water from one Coastal some part of the source water. Plain well, but not in water from the other six wells in which it Results of the water-quality analyses indicate that con- was detected. Carbon tetrachloride was detected in water from taminants are present at concentrations that exceed MCLs in three wells, exceeding the MCL (2µg/L) in water from one water from some of the wells sampled, and pH and constitu- well (030460) in a bedrock aquifer. ents exceed New Jersey SMCLs in water from several wells. The compound cis-1,2-dichloroethylene is a degradation In other wells, however, several constituents that are consid- product of PCE and TCE; its presence, therefore, indicates that ered contaminants were present at elevated levels that did not biodegradation of the parent compounds is occurring in the exceed established water-quality standards. aquifers. A further degradation product, vinyl chloride, was not detected in water from any of the sampled wells, however. 1

100 100

a b Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 New Jersey Drinking Water Standard = 70 micrograms per liter 10 10 MCL = 1 microgram per liter

1 1 PER LITER PER LITER 0.1 0.1

0.01 0.01 CONCENTRATION OF TCE, IN MICROGRAMS CONCENTRATION CONCENTRATION OF MTBE, IN MICROGRAMS OF MTBE, CONCENTRATION EXPLANATION 0.001 0.001 AQUIFER TYPE

270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402350083 270080270147270155270182390451050039 070177070368150207230195291264010039010600090136150276030301030460130098210402350083 Glacial WELL NUMBER WELL NUMBER

Unconfined Coastal Plain

Confined Coastal 100 100 Plain

c d Bedrock TTHM MCL = 80 micrograms per liter 10 10 MCL = 1 microgram per liter

1 1

PER LITER 0.1 0.1 MICROGRAMS PER LITER

0.01 0.01 CONCENTRATION OF CHLOROFORM, IN CONCENTRATION CONCENTRATION OF PCE, IN MICROGRAMS OF PCE, CONCENTRATION

0.001 0.001

270080270147270155270182390451050039 070177070368150207230195291264010039010600090136150276030301030460130098210402350083 270080270147270155270182390451050039 070177070368150207230195291264010039010600090136150276030301030460130098210402350083 WELL NUMBER WELL NUMBER

Figure 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. (MCL, maximum contaminant level; TTHM, total trihalomethanes; TTHM MCL is the sum of bromoform, bromodichloromrthane, dibromochloromethane, and chloroform concentrations) Quality of Source Water to Community Water-Supply Wells 17

Of the THMs, chloroform was detected in water from 12 10 wells completed in unconfined aquifers. Most detections were a at low concentrations (0.05-0.93 µg/L) in samples from nine of the wells, but this compound was present at a concentration 1 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 0.1 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 0.01 treated drinking water also are present in the untreated water.

Nutrients OF AMMONIA, IN MILLIGRAMS PER LITER CONCENTRATION 0.001

Nutrients is a term that includes compounds such as 270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402350083 ammonia, nitrate, and phosphate. Ammonia was not detected WELL NUMBER in water from wells in the bedrock and glacial aquifers, but was detected in water from all sampled wells in the Coastal 10 Maximum contaminant level = 10 milligrams per liter Plain aquifers (fig. 5a). Overall, water from wells in the b unconfined aquifers contained higher concentrations of ammonia than did water from wells in the confined aquifers; 1 the median concentrations were 0.54 and 0.16 mg/L, respectively. Concentrations of ammonia in water from the unconfined aquifers are a likely indication of anthropogenic inputs. The presence of ammonia in water from wells in the confined 0.1 aquifers is indicative of a nitrogen source in the aquifer, as the water tapped by these wells is too old to have been affected MILLIGRAMS PER LITER by human activities. Naturally occurring organic materials in 0.01 the sediments, which have been converted to lignite during the millions of years since deposition, are a likely source of IN OF NITRITE + NITRATE, CONCENTRATION nutrients. (The detections of orthophosphate in water from wells in the confined aquifers (app. 2) also could be indicative 0.001 of organic matter in the aquifers.) Reducing conditions exist 270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402350083 in the parts of the confined aquifers tapped by the sampled wells, as there is little if any DO present in the water; thus, WELL NUMBER the nitrogen in these aquifers is not oxidized to nitrate, but is present as ammonia. There is no New Jersey or Federal MCL EXPLANATION for ammonia in drinking water, but its presence in drinking AQUIFER TYPE water is of interest because, under oxidizing conditions, it can Glacial Confined Coastal be converted to nitrate. Plain Nitrite (as N) was detected in water from only one well in Unconfined Coastal Bedrock a glacial aquifer, at a concentration of 0.03 mg/L, which does Plain 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 Figure 5. Concentrations of (a) ammonia and (b) nitrite + nitrate detected in water from five of the six wells in unconfined in water from 20 community water-supply wells in New Jersey, by Coastal Plain aquifers and in water from all wells in bedrock aquifer type, 1998-99. and glacial aquifers. Concentrations of nitrate were less than the drinking water MCL of 10 mg/L as N in all samples; the concentrations in excess of 1 mg/L are indications of nitrogen highest concentrations—3.63 and 4.86 mg/L—were in water inputs by human activities. Using the latter criterion, water from wells in bedrock aquifers; one well in a Coastal Plain from all wells in the bedrock aquifers, from three of the five aquifer yielded water containing 3.19 mg/L (fig. 5b). Madison wells in glacial aquifers, and from two wells in the unconfined and Brunett (1985) indicate that concentrations of nitrate in Coastal Plain aquifers has been affected by inputs of nitrogen ground water that exceed 3 mg/L represent effects of human resulting from human activities. Although concentrations of activities, whereas Perlmutter and Koch (1972) state that nitrate were low in three other wells in unconfined Coastal 18 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Plain aquifers, concentrations of DO also were low (0.1 mg/L) 800-foot sand (a unit within the Kirkwood-Cohansey aquifer in water from those wells, and concentrations of ammonia system). Concentrations in water from four of the five wells were high (0.72-1.35 mg/L). Consequently, nitrate probably in glacial aquifers exceeded 50 mg/L; the concentrations of had been reduced (or ammonia never oxidized), and nitrogen chloride in one sample was 113 mg/L. Concentrations of chlo- inputs likely were in the range indicating human activities ride in water from three of the five wells in bedrock aquifers rather than natural conditions. exceeded 50 mg/L; the concentration in water from one well Concentrations of phosphate ranged from undetectable (030301) was 634 mg/L (fig. 6a), more than twice the SMCL (at 0.01 mg/L as P) to 0.29 mg/L as P. The highest concen- of 250 mg/L, and substantially higher than concentrations of trations were in water from wells completed in the confined chloride previously reported for ground water in northeastern Coastal Plain aquifers, the lowest (undetected) in water from New Jersey (Szabo and others, 1989). The concentrations of wells in three unconfined Coastal Plain aquifers (app. 2). The sodium in water from this well was 209 mg/L—more than materials that compose two of these latter unconfined Coastal 4 times the SMCL of 50 mg/L. Water from this well also Plain aquifers (the Kirkwood Formation and Cohansey Sand; contained concentrations of PCE and TCE that exceeded their and the Oldbridge Formation, part of the Potomac-Raritan- respective MCLs; clearly, contaminants from human activi- Magothy aquifer system) are primarily quartz sand with minor ties have affected the quality of water that is being withdrawn amounts of organic matter. The third, the unconfined updip from this well. These results indicate that anthropogenic inputs part of the Lower Potomac-Raritan-Magothy aquifer system, also could account for the elevated concentrations of sodium is also primarily quartz sand. Within this lower part of the and chloride. aquifer system, silt and clay layers contain sporadic occur- Concentrations of sodium in water from 15 of the 16 rences of organic materials, including woody fragments, but wells completed in unconfined aquifers, and 3 of the 4 wells in wells are unlikely to be completed in these layers. The other confined aquifers were less than 50 mg/L (fig. 6b). Water from Coastal Plain formations (Magothy, sand units of the Raritan, the well (150276) in the confined Potomac-Raritan-Magothy Lower Kirkwood) that form unconfined and confined aquifers aquifer system contained sodium at a concentration of 67.3 all contain carbonaceous materials (Owens and Sohl, 1969). mg/L, however, with a corresponding chloride concentration The highest concentrations of phosphate were in water from of 27.9 mg/L. Additionally, the concentration of fluoride in the downdip (confined) Lower Kirkwood aquifer, which con- water from this well was the highest (1.4 mg/L) measured in tains not only finely comminuted carbonaceous material, but the water sampled during this study; this concentration did not fossils that indicate a marine origin. Thus, it is likely that the exceed the MCL. The concentrations of fluoride in water from concentrations of phosphate in the Coastal Plain aquifers are well 150276 undoubtedly are derived from natural sources. mainly related to the abundance, or lack thereof, of naturally Concentrations of sulfate, with one exception, were occurring organic materials. less than 60 mg/L in water from wells in all the unconfined Concentrations of phosphate in water from wells com- aquifers and less than 20 mg/L in water from two Coastal pleted in the bedrock aquifers were low but detectable. The Plain wells in unconfined aquifers. The water from the wells soils developed on the bedrock formations are, for the most in confined Coastal Plain aquifers contained concentrations part, rich in clays to which anthropogenic phosphate from of sulfate at less than 20 mg/L. The highest concentration land-surface or subsurface sources would likely adsorb. Phos- (623 mg/L) was measured in water from a well (350083) in phorus apparently is present in these sedimentary formations, a northeastern New Jersey bedrock aquifer, and exceeded the because the mineral apatite (Ca5(PO4)3) is reported in contact- SMCL of 250 mg/L (fig. 6c; app. 2). In this aquifer (part of the metamorphosed rocks adjacent to diabase intrusions (Van Passaic Formation), concentrations of this magnitude are most Houten, 1969). The concentrations of phosphate in water from likely to be natural, resulting from dissolution of sulfate min- the bedrock wells may derive, at least in part, from naturally erals such as gypsum (Szabo and others, 1989). The concen- occurring materials. tration of calcium in the sample from this well also was high Concentrations of phosphate in water from the gla- (271 mg/L), supporting the likelihood that aquifer minerals cial-aquifer wells were in the same range (0.01-0.10 mg/L) (gypsum, in this case) substantially affect the chemistry of the as those in water from the bedrock wells. Both natural and ground water. anthropogenic sources are possible; assessing potential geo- Fluoride was detected in water from only one well in the logic inputs is complicated by the heterogeneous nature of bedrock aquifers, from two wells in unconfined Coastal Plain geologic sources for the glacial deposits. 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- Major and Minor Ions, Trace Elements, and pH centrations were greater than the MCL. Bromide was detected in water from all 18 wells for Concentrations of chloride in water from wells completed which it was analyzed. For the entire set of 20 wells, concen- in the Coastal Plain aquifers were all less than 50 mg/L; the trations of bromide tended to increase as concentrations of lowest concentrations (less than 10 mg/L) were in water from chloride increased (r2 = 0.38, p = 0.006); for wells in a par- three of the four wells completed in the confined Atlantic City ticular aquifer type, the relation was strongest for the wells in Quality of Source Water to Community Water-Supply Wells 19

confined Coastal Plain aquifers (fig. 7). The concentration of bromide can affect the concentration of the bromide-containing species of the THMs. 1000 Secondary maximum contaminant level = 250 milligrams per liter Concentrations of iron in water from the 20 wells ranged a widely—from less than the MRL (10 µg/L) to nearly 7,000 µg/L. Although soils and aquifer materials may contain sub- 100 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, 10 however. The highest concentrations of iron, which exceeded

MILLIGRAMS PER LITER the SMCL (0.3 mg/L), were in acidic water from four wells

CONCENTRATION OF CHLORIDE, IN CONCENTRATION in unconfined Coastal Plain aquifers where the concentrations

1 of DO (and nitrate) were low. Concentrations of iron in water from the confined Coastal Plain aquifers were at least an order 270080 270147270155270182390451050039070177070368150207230195291264 010039010600090136150276030301030460130098210402350083 of magnitude less than those in water from the unconfined WELL NUMBER Coastal Plain aquifers. Iron was not detected (reported as <10 µg/L) in water from all wells in the bedrock aquifers, one well 1000 in unconfined Coastal Plain aquifers, and two wells in glacial b aquifers; concentrations were estimated at less than 10 µg/L in Secondary maximum contaminant level = 50 milligrams per liter water from two other glacial-aquifer wells (app. 2). 100 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

10 0.25 MILLIGRAMS PER LITER CONCENTRATION OF SODIUM, IN CONCENTRATION

1 0.20 270080 270147270155270182390451050039070177070368150207230195291264 010039010600090136150276030301030460130098210402350083 WELL NUMBER

1000 0.15 c Secondary maximum contaminant level = 250 milligrams per liter

100 0.10 R2 = 0.38 p-value = 0.006

10 MILLIGRAMS PER LITER 0.05 CONCENTRATION OF SULFATE, IN OF SULFATE, CONCENTRATION BROMIDE CONCENTRATION, IN MILLIGRAMS PER LITER

270080 270147270155270182390451050039070177070368150207230195291264 010039010600090136150276030301030460130098210402350083 0.00 WELL NUMBER 1 10 100 1,000 EXPLANATION CHLORIDE CONCENTRATION, IN MILLIGRAMS PER LITER AQUIFER TYPE EXPLANATION

Glacial Confined Coastal AQUIFER TYPE Plain Glacial Confined Coastal Unconfined Coastal Bedrock Plain Plain Unconfined Coastal Bedrock Plain

Figure 6. Concentrations of (a) chloride, (b) sodium, and (c) Figure 7. Relation of concentrations of bromide to sulfate in water from 20 community water-supply wells in New concentrations of chloride in water from 20 community water- Jersey, by aquifer type, 1998-99. supply wells in New Jersey, 1998-99. 20 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 in the bedrock aquifers, one well in an unconfined Coastal 0.04 Plain aquifer, and four wells in glacial aquifers. Concentra- tions also were generally low (20 µg/L or less) in water from 0.035 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. 0.03 2). The high concentrations of manganese all exceeded the SMCL of 50 µg/L. 0.025 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 0.02 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 0.015 was outside the New Jersey optimum range for pH in drinking water (6.5-8.5; table 2). UV-254 ABSORBANCE, AS 1/CENTIMETERS UV-254 0.01

Organic Carbon 0.005

Concentrations of DOC in the ground-water samples were about the same as those of TOC, indicating that there 0.00 was little particulate organic matter present. Water from wells 270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402 350083 with high-volume output is less likely to be turbid (contain- WELL NUMBER ing particles) because there is less opportunity for particles to accumulate than in water from wells pumped only sporadi- EXPLANATION cally. Concentrations of both TOC and DOC were less than 2 AQUIFER TYPE mg/L in all samples, with the highest values being measured Glacial Confined Coastal Plain in water from several wells in unconfined Coastal Plain and glacial aquifers (app. 2). The sample from one glacial-aquifer Unconfined Coastal Bedrock Plain well (270147) contained not only high concentrations of DOC (1.40 mg/L), but several VOCs, with some concentrations Figure 8. Values of ultraviolet absorbance at 254 nanometers exceeding MCLs. (UV-254) in water from 20 community water-supply wells in New UV-254 values were generally higher in ground water Jersey, by aquifer type, 1998-99. from the Coastal Plain aquifers, both confined and unconfined, than those in water from the bedrock and glacial aquifers, a class of yellow-black decomposition products of plant and in some cases by an order of magnitude (fig. 8). Only for animal organic matter; they are refractory and resistant to deg- the sample from one glacial-aquifer well (270147) was the radation (Aiken, 1985). The physical and chemical characteris- UV-254 value comparable to the UV-254 measurements for tics of humic substances are, as yet, not well defined, but they samples from the Coastal Plain wells. 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 Dissolved Organic Carbon Fractions the basis of their solubility in dilute acids and bases. Fulvic acids are soluble at any pH; humic acids precipitate from and Disinfection By-Products aqueous solutions at a pH less than 2, and humin is insoluble at any pH. Both humic and fulvic acids are strong complexing DOC consists of a variety of compounds that can be agents; fulvic acid is a stronger reducing agent than is humic grouped by fractionation techniques on the basis of their acid (Thurman, 1985). Humic substances are hydrophobic, chemical behavior. Interactions of DOC and its groups of com- thus they are able to transport other organic contaminants that pounds with chlorine to form DBPs can be examined through also are hydrophobic (Wong and others, 2002). Moreover, laboratory incubation studies. 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 Organic Carbon Fractions are mostly removed, however, if water is treated with metal salts that coagulate much of the organic matter present (Wong Humic substances constitute the largest proportion of the and others, 2002). compounds that compose DOC. They are found in all terrestrial and aquatic environments. Humic substances constitute Dissolved Organic Carbon Fractions and Disinfection By-Products 1

Hydrophilic acids constitute the other major component nols (Larson and Weber, 1994). The rate of THM formation is of DOC; carbohydrates, carboxylic acids, and amino acids affected by chlorine concentration, bromide concentration, pH, are present in lesser amounts (Thurman, 1985). Hydrophilic and temperature (Adin and others, 1991). acids are a complex mixture of organic acids, and are mostly anionic, although some are uncharged. Because concentrations of DOC in the ground-water Formation of Disinfection By-Products During the samples were low (generally about 1 mg/L or less), differ- Laboratory Incubation Study ences in the DOC fractions in most water samples were small. Concentrations that differ by only 0.1 mg/L actually may not The concentration of THMs formed as a result of the be different, as there is some analytical error associated with disinfection of water supplies is known as the trihalomethane each determination. For water from the wells in Coastal Plain formation potential (THMFP) and is defined as the difference aquifers, concentrations of combined hydrophilic acids and in concentration measured after treatment and the concentra- neutrals, and low-molecular-weight hydrophilic compounds tion (if any) measured in the source water, as in the following (the XAD-8 effluent (passes through the XAD8 column)— equation: DOC 2) generally were as high as, or slightly higher than, THMFP = THM – THM (1) those of the hydrophobic acids (the XAD-8 eluate (retained treated water source water on the XAD-8 resin)—DOC 3). In samples from two wells (150207, 150276), however, concentrations of hydrophobic The concentrations of the THMs measured after a 7-day acids were slightly higher than concentrations of the combined incubation of the treated water samples (table 9) varied by hydrophilic/neutral/low-molecular weight fractions. In those about two orders of magnitude, depending in part on the initial samples where the hydrophilic acid fraction (passes through concentration of one or more THMs in the source water, but the XAD-8 and is retained on XAD-4 resin—DOC 6) was mostly on the chemical characteristics of the ground water, determined, however, concentrations of hydrophilic acids were which are derived, in part, from characteristics and materials less than those of hydrophobic acids (table 8). inherent to the aquifer from which the water was drawn. Concentrations of combined hydrophilic acids and neu- Although chloroform was detected in source water from trals and low-molecular-weight hydrophilic compounds (DOC 12 of the 20 wells sampled, most concentrations were less than 2) also were higher than those of hydrophobic acids (DOC 1 µg/L. Chloroform was not detected in source water from the 3) in water from wells in bedrock and glacial aquifers, with wells in confined aquifers or in four of the six Coastal Plain one exception (well 390451; table 8). In all water samples, wells in unconfined aquifers. Bromodichloromethane was the the hydrophobic neutral fraction (DOC 4) was negligible. only other THM detected in source water; it was present at Fractions DOC 5-7 were not determined for samples from the 0.5 µg/L in the sample containing the highest concentration of bedrock and glacial wells. 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, Disinfection By-Products higher concentrations of THMs tend to form in water from the Coastal Plain aquifers than from the other aquifers from which Sources samples were collected. Water from two wells in unconfined Coastal Plain aquifers contained total THMs at concentrations Formation of DBPs was attributed to the use of chlorine that exceed the Disinfection By-Product Rule MCL of 80 µg/L in drinking water for the first time in 1974 (Rook, 1974). The (table 1). DBPs are formed when organic matter in the water reacts Using data for all wells, the concentrations of THMs, with the chlorine (NaOCl) used to disinfect the water used for expressed as THMFP, tended to increase as UV-254 increased public supply against disease-causing water-borne organisms, (r2 = 0.59) (fig. 9). The trend is controlled mainly by data for such as E. coli, Cryptosporidium, and Giardia. When first wells in glacial and unconfined Coastal Plain aquifers; data for studied, natural organic matter was found to be an important the confined Coastal Plain and bedrock wells showed little or component of the organic material that reacted with chlorine no trend. Regarding data for wells in unconfined Coastal Plain to form DBPs (Stevens and others, 1976). The major chemical aquifers, concentrations of the individual THMs also tended to species formed by the chlorination are THMs, HAAs, HANs, increase as specific UV-254 absorbance (UV-254 normalized and chloral hydrate. Inorganic by-products, such as chlorates, to the concentration of DOC, or SUVA) increased (fig. 10a, b, also were found to form (Andrews and Ferguson, 1996). c, d); data for wells in other aquifer types showed no trend, or DBPs are formed in a series of steps involving oxida- positive or negative trends controlled by outliers. The relation tion of organic compounds and incorporation of chlorine (and between SUVA and chloroform (fig. 10c) was clearer; data for other halogens such as bromine) into the organic matter. The wells in both unconfined and confined Coastal Plain aquifers rates of these reactions vary. Studies indicate that some of the showed positive, but different trends. more likely organic compounds involved in the reactions that In 1998, USEPA promulgated a criterion of 2.0 L/mg-m produce DBPs (in particular, THMs) are diketones and phe- (liter per milligram-meter) for SUVA, which is calculated Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

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] Hydro- Hydro- Hydro- Low molecular Hydro- Hydro- Influent, philic acids, USGS phobic phobic weight com- philic philic Aquifer all fractions: neutrals, low well acids: neutrals: pounds: acids: neutrals: type DOC 11 molecular weight number DOC 31 DOC 41 DOC 51 DOC 61 DOC 71 (mg/L) compounds: DOC 21 (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L) 030301 BR 1.0 0.6 0.4 0 nf nf nf 030460 BR 1.0 0.6 0.3 0.1 nf nf nf 130098 BR 1.0 0.6 0.4 0 nf nf nf 210402 BR 0.7 0.5 0.4 2-0.2 nf nf nf 350083 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 nf 270147 GL 1.5 0.8 0.7 0 nf nf nf 270155 GL 0.8 0.6 0.3 2-0.1 nf nf nf 270182 GL 0.7 0.7 0.2 2-0.2 nf nf nf 390451 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 0.2 070177 CP 1.2 0.6 0.4 0.2 nf nf nf 070368 CP 1.1 0.7 0.6 2-0.1 0.2 0.2 0.3 150207 CP 1.6 0.7 0.8 2 0.1 0.5 0.3 2-0.2 230195 CP 1.5 0.8 0.7 0 0.4 0.2 0.2 291264 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 nf 010600 CCP 0.6 0.4 0.3 2-0.1 nf nf nf 090136 CCP 0.8 0.3 0.3 0.2 nf nf nf 150276 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.

SUVA (L/mg-m) = [UV-254 (1/cm)/DOC (mg/L)] (2) low concentrations of DOC—hence high SUVA). Water from x 100 (cm/m), one well (270147) completed in a glacial aquifer developed high concentrations of THMs, comparable to those in water for a supply system’s source water prior to, and after treat- from the Coastal Plain aquifers. The UV-254 measurement for ment (U.S. Environmental Protection Agency, 1998). SUVA the sample from that well was high (as was the concentration calculated for source water from 8 of the 20 wells equaled or of DOC); thus, the SUVA value for that sample was compa- exceeded the criterion (table 10). All but one of the eight wells rable to SUVA values calculated for samples from the Coastal is completed in a Coastal Plain aquifer. Plain aquifers. It appears that, with both higher THMFP and The magnitude of UV-254 is related, not only to con- higher SUVA values (tables 9 and 10), waters from the Coastal centration of DOC, but to the degree of aromaticity of the Plain aquifers generally contain more aromatic DOC and gen- compounds that make up DOC. Measurements of UV-254 erally are more prone to THM formation than water from most generally were larger in water from wells in the Coastal Plain of the other aquifers from which samples were drawn. This aquifers than from wells in the bedrock aquifers and most of indicates that, at a first approximation, measurements of UV- the wells in glacial aquifers. On the basis of the calculated 254 could be useful in predicting the potential of New Jersey SUVA value, (table 10) the DOC of Coastal Plain ground ground water for developing THMs. waters contains more aromatic compounds, in general, than Of the THMs formed after chlorination, bromodichloro- does the DOC in water from the glacial or bedrock aquifers methane (CHBrCl2), chloroform (CHCl3), and dibromochlo- from which water samples were collected. Only one bedrock romethane (CHBr2Cl) generally were present at comparable well (030301) yielded water of substantial aromaticity (but concentrations (table 9). Concentrations of bromoform Dissolved Organic Carbon Fractions and Disinfection By-Products

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 characteristic in the U.S. Geological Survey National Water Information System (NWIS) database.] Bromodi- Dibromo- chloro Bromoform Chloroform chloro- USGS Total Bromide Aquifer methane (CHBr ) (CHCl ) methane THMFP well 3 3 THMs (mg/L) type (CHBrCl ) (µg/L) (µg/L) (CHBr Cl) (µg/L) number 2 2 (µg/L) (71870) (µg/L) (99307) (99304) (µg/L) (99305) (99306) 030301 BR 7.7 5.7 4.8 8.5 27 27 0.19 030460 BR 5.7 2.5 6.5 4.9 20 17 0.058 130098 BR 4.4 3.1 2.6 5.6 16 15 0.18 210402 BR 6.7 3.7 4.9 6.3 22 22 0.083 350083 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 0.048 270147 GL 15 1.1 29 7.9 53 53 0.043 270155 GL 5.8 2.5 7.5 5.4 21 17 0.053 270182 GL 2.8 1.1 2.2 2.8 8.9 8.9 0.062 390451 GL 9.4 1.8 6.5 8.2 26 25 0.086

050039 CP 9.1 0.4 54 3.8 67 29 0.045 070177 CP 15 1.0 17 7.1 40 40 0.12 070368 CP 3.7 1.0 6.2 2.2 13 13 0.051 150207 CP 40 5.9 32 30 110 110 0.15 230195 CP 29 2.2 35 17 83 83 nd 291264 CP 17 0.4 34 5.8 57 56 nd

010039 CCP 8.6 0.2 31 3.2 43 43 0.021 010600 CCP 8.8 <0.1 30 2.3 41 41 0.026 090136 CCP 14 1.9 22 10 48 48 0.036 150276 CCP 17 1.7 18 12 49 49 0.11

(CHBr ) were consistently lower than those of the other THMs 3 chlorinated samples from the community water-supply wells formed; water from several bedrock aquifers developed higher are actually slightly lower than reported. concentrations than did water from most of the other aqui- The chlorine added to disinfect water oxidizes bromide fer types. Overall, concentrations of CHBr Cl and CHBrCl 2 2 to hypobromous acid, which reacts with components of DOC generally increased as concentrations of DOC increased (fig. to produce the bromine-containing DBPs (Liang and Singer, 11a, b), with the trend largely controlled by relations between 2003). The concentrations of CHBr formed in the treated DOC and concentrations of the brominated compounds in 3 water samples from 18 of the community water-supply wells water from glacial and the Coastal Plain aquifers. Relations increased as the concentrations of bromide in the untreated between CHBr and DOC were unclear; only data for the 3 (source) water increased (bromide was not measured in unconfined Coastal Plain wells showed a discernible positive samples from two wells); the individual trends for samples linear trend (not illustrated). Regarding the data for all wells, from the different aquifer types were all generally positive virtually no relation was observed for the CHCl formed after 3 (fig. 12a). Relations with source-water bromide were less treatment and concentration of DOC (fig. 11c); CHCl in water 3 strong for the other two bromine-containing THMs, CHBr Cl from confined Coastal Plain aquifers showed a negative trend 2 (fig. 12b) and CHBrCl (not shown). The masses of bromide in with concentration of DOC. Concentrations of CHCl in the 2 3 the source-water samples are sufficient to produce the amounts incubated samples are considered with caution, however, as of bromine-containing THMs measured in the chlorinated and this compound was detected in all four blanks chlorinated in incubated samples. 1998 and 1999. It is likely that concentrations of CHCl in the 3 Concentrations of HAAs were, in general, lower by factors of 2 to 3 than those of the THMs. As with the THMs, Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

120 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 100 acid for samples from wells in the different aquifer types were generally unclear or dominated by outliers. Concentrations of HANs were undetected in water 2 80 R = 0.59 from several wells. Concentrations of individual HANs were p-value = 0.000 generally less than 4 µg/L. Concentrations of dibromoacetonitrile generally were similar to or slightly higher than those of bromochloroacetonitrile and substantially higher than the 60 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 40 availability of bromide than that of chlorine. Overall, concen-

THMFP, IN MICROGRAMS PER LITER trations of HANs were substantially lower than those of THMs and HAAs; higher concentrations of HANs tended to develop

20 in water from Coastal Plain wells.

Formation of Disinfection By-Products in 0 0 0.01 0.02 0.03 0.04 Dissolved-Organic-Carbon Fractions UV-254 ABSORBANCE, IN 1/CENTIMETERS Solutions of DOC fractions in water from some or all of the 20 wells were chlorinated and incubated for seven days: EXPLANATION fractions DOC 2 (hydrophilic organic acids and neutrals, AQUIFER TYPE and low-molecular-weight hydrophilic compounds), DOC 3 Glacial Confined Coastal (hydrophobic organic acids), and DOC 6 (hydrophilic organic Plain acids) were determined. Fraction DOC 6 was not isolated in Unconfined Coastal Bedrock water from the bedrock and glacial wells or six of the Coastal Plain Plain wells; therefore, only the DOC 3 fractions from these wells were chlorinated and incubated. DOC 2 fractions for Figure 9. Relation of trihalomethane formation potential (THMFP) several Coastal Plain wells also were not chlorinated and incu- to ultraviolet absorbance at 254 (UV-254) nanometers in water bated (table 13). In treated DOC fractions from those selected from 20 community water-supply wells in New Jersey, 1998-99. wells in the Coastal Plain aquifers, concentrations of THMs and HAAs were higher in the DOC 3 fraction, which contains however, concentrations of HAAs were higher in water from the hydrophobic humic substances, than in the DOC 6 frac- wells in the Coastal Plain than in water from wells in bedrock tion, which contains the hydrophilic humic acids (table 13). or glacial aquifers, with few exceptions (table 11). Concentra- (Liang and Singer (2003) obtained similar results for selected tions of HAAs in water from well 210402 in a bedrock aquifer surface-water drinking supplies.) Concentrations of HANs were comparable to those in water from the Coastal Plain were negligible in all fractions in which they were determined. wells, as were those in water from well 270147 in a glacial In samples from the bedrock and glacial wells, however, aquifer. Water from this latter well also developed high con- concentrations of total THMs in the DOC 3 and DOC 2 frac- centrations of THMs (and contained VOCs at concentrations tions were generally comparable, within a few micrograms per exceeding MCLs). Of the various HAAs, concentrations of the liter. Concentrations of total HAAs were slightly higher in the more highly chlorinated acids were highest; there were few DOC 3 fraction than in the DOC 2 fraction in samples from detections of monochloroacetic acid. Because of detections of bedrock wells and substantially higher (by factors of 1.5 to 4) HAAs in field blanks that were chlorinated and incubated in in samples from confined Coastal Plain aquifers. the laboratory at EHL, concentrations of these compounds in Concentrations of total HANs generally were higher in the the treated samples from the community water-supply wells DOC 2 fraction than the DOC 3 fraction except for sam- are viewed with caution. ples from glacial aquifers. Overall, concentrations of total Concentrations of the bromine-containing HAAs were THMs were substantially higher in the DOC 3 fraction comparable to those of the highly chlorinated HAAs in water (the hydrophobic acids) from Coastal Plain water samples from most of the wells in bedrock and glacial aquifers, but (median = 31.6 µg/L) than in the same fraction from bedrock tended to be lower than those of the highly chlorinated HAAs and glacial water samples (respective medians = 16.3 and 15.7 in water from the Coastal Plain wells. For all wells, relations µg/L). The total THM concentration in the DOC 3 fraction of between concentrations of bromine-containing HAAs such as the sample from glacial well 270147 was large (35.2 µg/L), 7 45

a 40 b 6

35 5 30

4 25

3 20 PER LITERS PER LITERS

15 2 10

1 CHBr3 CONCENTRATION, IN MICROGRAMS 5 EXPLANATION CHBrCl2 CONCENTRATION, IN MICROGRAMS AQUIFER TYPE 0 0 0 2 4 6 8 0 2 4 6 8 Glacial SUVA, IN LITERS PER MILLIGRAM-METER SUVA, IN LITERS PER MILLIGRAM-METER Unconfined Coastal Plain

Confined Coastal Dissolved Organic Carbon Fractions and Disinfection By-Products 60 35 c d Plain 30 50 Bedrock

25 40

30 15 PER LITERS PER LITERS

20 10

10 5 CHCl3 CONCENTRATION, IN MICROGRAMS CHBr2Cl CONCENTRATION, IN MICROGRAMS

0 0 0 2 4 6 8 0 2 4 6 8

SUVA, IN LITERS PER MILLIGRAM-METER SUVA, IN LITERS PER MILLIGRAM-METER

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

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. ]

UV-2541 UV-2543 USGS well SUVA2 USGS well SUVA2 Aquifer type (1/cm) Aquifer type (1/cm) number (L/mg-m) number (L/mg-m) (50624) (50624) 030301 BR 0.0074 3.5 050039 CP 0.007 1.4 030460 BR 0.0074 0.78 070177 CP 0.010 1.4 130098 BR 0.0072 0.78 070368 CP 0.018 1.6 210402 BR 0.0064 0.60 150207 CP 0.028 2.0 350083 BR <0.035 -- 230195 CP 0.035 3.5 270080 GL 0.0075 1.0 291264 CP 0.016 2.0 270147 GL 0.022 1.6 010039 CCP 0.024 6.0 270155 GL 0.0069 1.2 010600 CCP 0.027 6.7 270182 GL <0.004 -- 090136 CCP 0.028 5.6 390451 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. however. Chemical characteristics of water from this glacial the experimental results for the incubation studies of surface well generally were similar to those of waters from the Coastal water by Liang and Singer (2003). Plain wells, and thus the response to chlorination and incuba- HAA formation in the same samples generally followed tion apparently was similar. The presence of VOCs (primarily a similar pattern, but the concentrations were, overall, much TCE) at elevated levels in water from this well also could have lower. There were fewer detections of the brominated HAAs affected the propensity to develop DBPs. (bromochloroacetic acid (BrClAA) and dibromoacetic acid (Br2AA)) in water from glacial and bedrock aquifers than in water from unconfined Coastal Plain aquifers (appendix 3). Laboratory Determined Formation Rates of Br2AA never developed in water from two wells, one in a Disinfection By-Products in Treated Water from glacial aquifer and one in a confined Coastal Plain aquifer. Community Water-Supply Wells BrClAA never developed in water from the same well in the glacial aquifer. Monochloroacetic acid (ClAA) seldom formed Because the residence time of treated water in distribu- at detectable levels in any of the samples. Concentrations of tion systems is variable, rates of formation of disinfection dichloroacetic acid (Cl2AA) and trichloroacetic acid (Cl3AA) by-products in treated-water samples were assessed. Water not only were substantially higher in samples from wells in the samples from seven wells (two each completed in bedrock, Coastal Plain aquifers than in samples from wells in bedrock glacial, and unconfined Coastal Plain aquifers, and one in a or glacial aquifers, these compounds appeared to develop confined Coastal Plain aquifer) were chlorinated and incu- more rapidly, particularly in samples from wells 230195 and bated for 6 hours, 24 hours, and 168 hours (7 days) at 010600 (app. 3). Concentrations of several HAAs remained 25 °C at the EHL laboratory. The concentrations of THMs below the MDL (<0.1 µg/L) after 6 hours of incubation in that developed over time in water from the Coastal Plain wells samples from three wells (390451, 350083, and 270155) in were substantially higher than those in water from the wells in bedrock and glacial aquifers. Where detected, HAAs in sam- glacial aquifers, which were higher than those in water from ples from these and the other wells in these aquifers changed the bedrock aquifers (fig. 13a, b, c; app. 3). As concentrations little between 6 and 24 hours of incubation. Concentrations of increased over the 168 hours, the rate of THM formation was THMs in samples from all the wells increased throughout the more rapid over the period from 6 to 24 hours (with concen- incubation period, however, typically doubling by 24 hours in trations nearly doubling in most cases) than it was from 24 samples from the wells in Coastal Plain aquifers. The rate of hours to 168 hours. Such a decrease in formation rate would HAA formation (more HAAs formed during the first 24 hours be expected, as the concentrations of reactants (DOC, Br, and of incubation than subsequently) appeared to be rapid in some NaOCl) decrease over time. These results are consistent with samples (fig. 14a), whereas more THMs developed between 24 and 168 hours in some samples (fig. 13b). As reported by Dissolved Organic Carbon Fractions and Disinfection By-Products

45 7.0

40 a a 6.0 35 R2 = 0.49 5.0 30 p-value = 0.002

25 4.0

20 3.0 PER LITER

CONCENTRATION, IN 15 2 2.0 10 MICROGRAMS PER LITER

CHBrCl 1.0 5 CONCENTRATION, IN MICROGRAMS 3

0 0.0 0 0.5 1 1.5 CHBr 0.00 0.05 0.10 0.15 0.20 0.25 DOC CONCENTRATION, IN MILLIGRAMS PER LITER BROMIDE CONCENTRATION, IN MILLIGRAMS PER LITER

35 35.0 b 30 b 30.0 25 25.0 20 2 20.0 R = 0.21 15 p-value = 0.056 15.0

Cl CONCENTRATION, IN 10 2 Cl CONCENTRATION, IN

2 10.0 MICROGRAMS PER LITER

5 MICROGRAMS PER LITER CHBr

CHBr 5.0 0 0 0.5 1 1.5 0.0 0.00 0.05 0.10 0.15 0.20 0.25 DOC CONCENTRATION, IN MILLIGRAMS PER LITER BROMIDE CONCENTRATION, IN MILLIGRAMS PER LITER 40

35 c EXPLANATION AQUIFER TYPE 30 Glacial Confined Coastal 25 Plain

20 Unconfined Coastal Bedrock Plain 15 CONCENTRATION, IN 3 10 Figure 12. Relation of concentrations of (a) bromoform (CHBr3) MICROGRAMS PER LITER

CHCl and (b) dibromochloromethane (CHBr Cl) in chlorinated water to 5 2 concentrations of bromide in source water from 20 community 0 water-supply wells in New Jersey, 1998-99. 0 0.5 1 1.5

DOC CONCENTRATION, IN MILLIGRAMS PER LITER Liang and Singer (2003), other researchers have found that EXPLANATION HAAs form more rapidly than do THMs; the results in this study indicate that rates of formation of the THMs and HAAs AQUIFER TYPE were variable. Glacial Confined Coastal Of the HANs, trichloroacetonitrile (Cl3AN) was detected Plain in no samples, regardless of incubation time. Dichloroace- Unconfined Coastal Bedrock tonitrile (Cl2AN) formed during the three incubation times Plain in sample sets from the two wells (230195 and 150207) in unconfined Coastal Plain aquifers, and was detected in one Figure 11. Relation of concentrations of (a) of three samples in the sets from a well in a bedrock aquifer bromodichloromethane (CHBrCl ), (b) dibromochloromethane 2 (210402) and the well in a confined Coastal Plain aquifer (CHBr Cl), and (c) chloroform (CHCl ) in chlorinated water to 2 3 (010600) (app. 3). The brominated HANs, bromochloroaceto- concentrations of dissolved organic carbon (DOC) in source water nitrile (BrClAN) and dibromoacetonitrile (Br AN), formed in from 20 community water-supply wells in New Jersey, 1998-99. 2 2 8

100 100 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 a b

10 10 PER LITER PER LITER 1 1 CONCENTRATION, IN MILLIGRAMS CONCENTRATION, CONCENTRATION, IN MICROGRAMS CONCENTRATION,

0.1 0.1

CHBr3 CHBr2Cl CHBrCl2 CHCl3 CHBr3 CHBr2Cl CHBrCl2 CHCl3

WELL 230195 - UNCONFINED COASTAL PLAIN WELL 390451 - GLACIAL

100 c

EXPLANATION 10 INCUBATION TIME

6 hours 24 hours PER LITER 1 168 hours CONCENTRATION, IN MICROGRAMS CONCENTRATION,

0.1

CHBr3 CHBr2Cl CHBrCl2 CHCl3

WELL 350083 - BEDROCK

Figure 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. (CHBr3, bromoform; CHBr2Cl, dibromochloromethane; CHBrCl2, bromodichloromethane; CHCl3, chloroform). Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types 9

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.] Bromo- Mono- Dibromo- Dichloro- Trichloro- chloro- chloro- acetic acid acetic acid acetic acid USGS well acetic acid acetic acid Total HAAs Aquifer type (Br AA) (Cl AA) (Cl AA) number (BrClAA) 2 2 (ClAA) 3 (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (99312) (99309) (99310) (99322) (99308) 030301 BR 2.1 1.9 2.5 <0.1 1.9 8.4 030460 BR 1.5 1.4 1.6 <0.1 1.4 5.9 130098 BR 1.2 1.5 <0.1 <0.1 1.3 4.0 210402 BR 3.2 3.7 3.2 3.8 1.7 16 350083 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 9.9 270147 GL 5.3 2.2 12 2.3 9.6 31 270155 GL 2.3 2.5 2.1 2.8 1.7 11.4 270182 GL 1.2 <0.1 1.5 <0.1 1.7 4.4 390451 GL 2.3 1.5 2.4 <0.1 1.8 8.0 050039 CP 2.5 11 5.5 <0.1 2.7 22 070177 CP 3.1 1.4 6.9 <0.1 4.0 15 070368 CP 2.2 1.2 8.3 <0.1 4.8 17 150207 CP 9.3 6.1 9.6 <0.1 6.9 32 230195 CP 8.5 4.1 15 2.3 13 43 291264 CP 3.1 1.0 10 <0.1 7.0 21 010039 CCP 3.4 <0.1 14 <0.1 18 35 010600 CCP 2.5 <0.1 9.8 <0.1 4.0 16 090136 CCP 4.0 2.5 6.7 <0.1 3.2 16 150276 CCP 5.1 2.4 9.5 <0.1 6.9 24 the sample sets from most of the wells, with the highest con- Possible Bias in Disinfection By-Product Data centrations developed in water from the unconfined Coastal Plain aquifers. The formation rate generally was greatest dur- The actual concentrations of the various DBPs in chlori- ing the first 6 hours of incubation, with relatively little change nated and incubated water samples from the 20 wells could be in concentration occurring during the period from 24 to 168 biased high because THMs and HAAs were detected in treated hours of incubation. 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- Differences in Disinfection By-Product cate that the concentrations of the DBPs measured in treated water from wells in the Coastal Plain aquifers (sampled during Formation Potential in Water from 1998) are not biased high because the contaminated blank water was not part of the processing of samples. Thus the dif- Different Aquifer Types ference in concentrations of DBPs in water samples from the Coastal Plain aquifers and those from the bedrock and glacial The differences observed in DBP formation potentials aquifers may be at least as large as that shown by the data. can result from various causes. Relations among the observed Furthermore, the concentrations of DBPs in the treated blanks DBP formation potentials can be affected by bias in the data are lower than those that formed in many of the environmental and the origins of factors, primarily concentrations of constitu- samples, primarily those from Coastal Plain aquifers. Should ents, that could affect how DBPs form. there be a systematic and uniform bias in the data caused by laboratory contamination, as opposed to contaminated blank 30 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

100 Table 12. Concentrations of haloacetonitriles in chlorinated a 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, 10

haloacetonitriles. Number in parentheses is parameter code used to identify PER LITER the constituent, property, or characteristic in the U.S. Geological Survey National Water Information System (NWIS) database.]

Bromo- Dibromo- Dichloro- IN MICROGRAMS CONCENTRATION, chloro- acetoni- acetoni- 1 USGS acetoni- Total Aquifer trile trile Br2AA BrCIAA CIAA CI2AA CI3AA well trile HANs type (Br AN) (Cl AN) number (BrClAN) 2 3 (µg/L) WELL 390451 - GLACIAL (µg/L) (µg/L) (µg/L) (99316) (99314) (99315) 100 030301 BR 0.7 1.3 <0.1 2.0 b 030460 BR 0.7 1.2 <0.1 1.9 130098 BR 0.6 1.1 <0.1 1.7 210402 BR 0.6 1.0 <0.1 1.6 350083 BR 0.6 <0.1 <0.1 0.6 10 270080 GL <0.1 0.6 <0.1 0.6 270147 GL 0.9 0.7 0.5 2.1 PER LITER 270155 GL 0.6 0.9 <0.1 1.5 270182 GL <0.1 <0.1 <0.1 <0.1

390451 GL 1.5 1.5 <0.1 3.0 IN MICROGRAMS CONCENTRATION, 1 050039 CP 0.5 1.0 <0.1 1.5 Br2AA BrCIAA CIAA CI2AA CI3AA 070177 CP <0.1 1.1 <0.1 1.1 070368 CP 0.9 0.8 0.8 2.5 WELL 230195 - UNCONFINED COASTAL PLAIN 150207 CP 3.7 5.0 1.2 9.9 230195 CP 3.0 3.1 2.0 8.1 EXPLANATION 291264 CP <0.1 1.1 <0.1 1.1 INCUBATION TIME 010039 CCP <0.1 <0.1 <0.1 <0.1 6 hours 010600 CCP <0.1 <0.1 <0.1 <0.1 24 hours 090136 CCP 12 <0.1 <0.1 12 168 hours 150276 CCP 0.7 1.6 <0.1 2.3 Figure 14. Haloacetic acid formation over time in water from (a) well 390451, completed in a glacial aquifer, and (b) well water, the relations between concentration and groups of wells 230195, completed in a Coastal Plain aquifer in New Jersey,

(by aquifer type) could still be valid. 1998-99. (Br2AA, dibromoacetic acid; BrClAA, bromochloroacetic

acid; ClAA, cloroacetic acid; Cl2AA, dichloroacetic acid; Cl3AA, trichloroacetic acid) Relations Among Disinfection By-Product Formation Potentials is treated. The total concentrations of HAAs, which probably represent the HAAFP (fig. 16), were distributed among the With few exceptions, the THMFP for water from the aquifer types in a pattern similar to that of the THMFP, and Coastal Plain aquifers was greater (by factors of 1.5 to 4) than there was a strong positive linear relation (r2 = 0.65) between that for water in bedrock and glacial aquifers (fig. 15). A true THMFP and concentrations of total HAAs (fig. 17). Relations haloacetic acid formation potential (HAAFP) could not be between total HANs and THMs (r2 = 0.39), and total HANs calculated, however, because HAAs were not measured in and total HAAs (r2 = 0.11) were substantially weaker. 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 Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types 1

Table 13. 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, haloacetonitriles; 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 Aquifer DOC 31 DOC 61 DOC 21 DOC 31 DOC 61 DOC 21 DOC 31 DOC 61 DOC 21 well type (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) number 030301 BR 22.0 nf 19.1 21.6 nf 13.7 0.0 nf 0.6 030460 BR 16.1 nf 14.4 20.1 nf 18.2 0.0 nf 0.6 130098 BR 12.7 nf 15.1 16.1 nf 8.4 0.2 nf 0.8 210402 BR 16.5 nf 19.2 21.1 nf 11.5 0.2 nf 1.0 350083 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 0.0 270147 GL 35.2 nf 32.2 31.9 nf 20.6 0.4 nf 1.6 270155 GL 15.7 nf 14.5 16.3 nf 10.8 0.3 nf 0.3 270182 GL 9.6 nf 10.2 7.3 nf 8.7 nf nf 0.0 390451 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 nf 070177 CP 29.3 nf 29.4 26.0 nf 31.0 0.0 nf 0.0 070368 CP 31.4 14.8 nf 35.3 8.8 nf 0.0 0.0 nf 150207 CP 54.5 15.5 nf 44.7 14.5 nf 0.0 0.0 nf 230195 CP 59.5 16.1 nf 67.1 16.9 nf 0.0 0.0 nf 291264 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 nf 010600 CCP 32.9 nf 9.6 39.9 nf 7.4 0.0 nf 0.0 090136 CCP 27.2 nf 17.8 30.7 nf 9.4 0.0 nf 0.7 150276 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.

Origins of Selected Chemical Characteristics Coastal Plain wells) dominate, and the r2 for the entire data and Constituents and Their Effects on set is low (0.19). Linear relations are not apparent for the data Disinfection By-Product Formation Potential points for wells grouped by aquifer type except those for wells completed in glacial aquifers. A stronger linear relation is pres- Several factors potentially can affect DBP formation ent between UV-254 in untreated water and THMFP (shown in potentials. These include concentrations and characteristics of fig. 9), and the strongest relation is between UV-254 and total DOC, and concentrations of bromide. Concentrations of iron, HAA concentration (fig. 19). Thus, it appears that the aromatic manganese, and ammonia, which may be indicative of redox character of the DOC is an important factor in determining the conditions, presence of colloids, or complexation with organic DBP formation potential in ground water in New Jersey. matter, also could be factors. The origins of these constituents, DOC in ground-water samples from the Coastal Plain and the conditions under which they are present, vary among is, for most samples, more aromatic than the DOC in samples the aquifers studied. from the bedrock and glacial aquifers, as indicated by SUVA calculations as well as the UV-254 measurements. The hydrophobic fraction of DOC (DOC 3), which includes humic sub- Dissolved Organic Carbon stances, contains more aromatic compounds than the hydrophilic fraction. Concentrations of fraction DOC 3 were, in four The amount of DOC present in the water is not the only of six samples from unconfined Coastal Plain aquifers, about determining factor in DBP formation potential. Although there twice as high as those in samples from bedrock or glacial aqui- is a semblance of a positive relation between concentrations fers (table 8). Higher concentrations of DBPs developed in the of DOC and THMFP, using data for all wells (fig. 18), the two DOC 3 fractions in samples from the unconfined Coastal Plain highest concentrations of THMFP (for water samples from Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

than in DOC 3 fractions in samples from bedrock and glacial 120 aquifers. For samples from the unconfined Coastal Plain aquifers, relations of both total THMs and total HAAs in the DOC 2 3 fraction with SUVA were strong (r = 0.58 and 0.68, respec- 100 tively). Overall, the data indicate that DOC, particularly the Maximum contaminant hydrophobic acids, in unconfined Coastal Plain ground water level = 80 micrograms per liter is more aromatic than those in water from the bedrock and 80 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 60 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 40 neutral compounds) (table 13). Relations of THMs in samples IN MICROGRAMS PER LITER THMFP, from the confined Coastal Plain aquifers with SUVA show a virtually flat trend, although SUVA values, indicating aroma- 20 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 0 of the THMs and HAAs. Apparently, HAN development is not promoted by greater aromaticity. 270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402 350083 Within the hydrophobic fraction, the proportions of WELL NUMBER aromatic and aliphatic compounds can vary substantially, EXPLANATION arising from the origin of the DOC. Pomes and others (2000) indicate that aquatic humic substances with a predominance AQUIFER TYPE of aromatic compounds derive from terrestrial plant sources, Glacial Confined Coastal and those with a predominance of aliphatic compounds derive Plain from algal or bacterial sources. If most of the DOC present in Unconfined Coastal Bedrock ground water from a given aquifer is derived from materials Plain within the aquifer matrix or matrixes through which recharge passes, then it appears likely that the age and geologic set- Figure 15. Trihalomethane formation potential (THMFP) in water ting in which the aquifer materials were formed could have from 20 community water-supply wells in New Jersey, by aquifer a bearing on how strong an effect DOC has as a precursor type, 1998-99. to DBP formation. Younger (Late Paleozoic to Cenozoic) sediments in which land-plant remains are present would be clay bed (Zapecza, 1989). Plant material and phytoplankton likely to contain water with more aromatic DOC and, prob- would likely have been abundant in the marginal-marine (with ably, a higher potential for DBP formation than older (early the Mesozoic equivalent of mangrove swamps) and Cenozoic Paleozoic) sediments, particularly if the aquifers are confined. deltaic environments in which these Cretaceous and Tertiary (DOC in water from aquifers composed of fractured igneous sediments were deposited. and metamorphic rocks would be derived only from the land Only one well (270147) completed in a glacial aquifer surface in recharge.) yielded water with a comparably high DBP formation poten- The aquifers sampled during the present study are all tial. Some of the morainal deposits in northern New Jersey sedimentary in origin; the water samples with the highest DBP contain peat (Minard and Rhodehamel, 1969). Organic materi- formation potentials (THMFP, total HAAs, and HANs), with als in sediment could supply precursor DOC for DBP forma- few exceptions, come either from deep confined Coastal Plain tion in water from parts of some of the glacial aquifers. aquifers or unconfined Coastal Plain aquifers (the Potomac- The other, obvious source of DOC in the unconfined Raritan-Magothy and Kirkwood-Cohansey aquifer systems). aquifers is land-surface inputs to recharge from both natural The sediments of the Potomac-Raritan-Magothy aquifer and anthropogenic sources. Plant materials at land surface system contain lignite; these identifiable plant remains occur could be the major source of natural DOC in recharge waters. as dispersed fragments and in thin layers, particularly in the Anthropogenic sources of carbon compounds in recharge upper part of the system. Sediments of the Kirkwood-Cohan- could include septic systems, composting facilities, and vari- sey aquifer system contain fine-grained carbonaceous mate- ous land-surface and subsurface discharges of VOCs. rial, in dark-gray clays and dark, sometimes fossiliferous, silts For those water samples from the 20 wells that contained (Owens and Sohl, 1969). Where the aquifer is confined, Lower detectable VOCs, neither MTBE nor PCE concentrations Kirkwood sediments are overlain by a thick diatomaceous Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types

45 50

40 45

35 40

30 35

25 30

20 25 R2 = 0.65 p-value = 0.000 15 20

TOTAL HAAs, IN MICROGRAMS PER LITER TOTAL 10 15

5 10 TOTAL HAA CONCENTRATION, IN MICROGRAMS PER LITER 0 5

270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402 350083 0 WELL NUMBER 0 20 40 60 80 100 120 THMFP, IN MICROGRAMS PER LITER EXPLANATION AQUIFER TYPE EXPLANATION

Glacial Confined Coastal AQUIFER TYPE Plain Glacial Confined Coastal Unconfined Coastal Bedrock Plain Plain Unconfined Coastal Bedrock Plain Figure 16. Total haloacetic acids (HAAs) in water from 20 community water-supply wells in New Jersey, by aquifer type, Figure 17. Relation of total haloacetic acid concentration (HAA) 1998-99. (Maximum contaminant level = 60 micrograms per liter) to trihalomethane formation potential (THMFP) in treated water from 20 community water-supply wells in New Jersey, 1998-99. showed any relation to THMFP. The highest concentrations of TCE were present in two samples with high THMFP, but rela- concentrations of DOC than would water from deep wells (or tions between TCE and THMFP were neither strongly positive wells with deep open intervals), because shallow ground water nor linear. Although, it is possible that degradation of VOCs in unconfined aquifers typically is more susceptible to con- can contribute to DBP precursor carbon, it also is possible that tamination from the land surface than is deeper ground water. the presence of VOCs only indicates that the ground water Although the water tapped by the wells in unconfined aquifers contains various constituents (which could include DOC) in this study contains constituents, mostly VOCs, that clearly derived recently from the land surface. are derived from human activities at the land surface, there is Neither TOC nor DOC concentrations in water from no unequivocal evidence of large inputs of DOC or TOC from the 20 community water-supply wells were related to depth the land surface to most of the wells in unconfined aquifers. to the top of the open interval of the wells or to well depth. Of the two wells (270147 and 150207) that yielded water with Shallow wells (those completed at less than100 ft below land the highest concentration of DOC (1.4 mg/L), water from the surface) and those with open intervals at shallow depths gener- former well contained several VOCs, some at concentrations ally yielded water with concentrations of carbon less than exceeding MCLs. Water from the latter well contained a barely 1 mg/L, as did many of the deeper wells. In water from the detectable level of 1,2-dichloroethane. A third well (070177) unconfined aquifers, concentrations of TOC tended to increase yielded water with 10 µg/L of cis-1.2-dichloroethylene and 43 with increasing depth to the open interval, and the highest µg/L of TCE, but the DOC in this water was only 0.70 mg/L. concentrations of DOC were in water from wells completed at Consequently, DOC level is not a useful measure of the source 115 and 282 ft (wells 270147 and 150207, respectively). It is of the DOC. likely that, were the organic carbon of mostly anthropogenic For most of the wells in unconfined aquifers, con- origin, water from the shallowest wells (or from those with centrations of DOC generally appear to be typical of those open intervals at the shallowest depths) would contain higher determined previously for ground water in those aquifers. Consequently, although some inputs of organic carbon may be Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

120 50

100 40

30 R2 = 0.19 p-value = 0.054 60 R2 = 0.60 p-value = 0.000 20

40 THMFP, IN MICROGRAMS PER LITER

10 20 TOTAL HAA CONCENTRATION, IN MICROGRAMS PER LITER

0 0 0.0 0.2 0.4 0.6 0.8 1.0 1.2 1.4 1.6 0.00 0.01 0.02 0.03 0.04

DOC CONCENTRATION, IN MILLIGRAMS PER LITER UV-254, IN 1/CENTIMETERS

EXPLANATION EXPLANATION AQUIFER TYPE AQUIFER TYPE Glacial Confined Coastal Glacial Confined Coastal Plain Plain Unconfined Coastal Bedrock Unconfined Coastal Bedrock Plain Plain

Figure 18. Relation of dissolved organic carbon (DOC) Figure 19. Relation of total haloacetic acid (HAA) concentration concentration to trihalomethane formation potential (THMFP) to ultraviolet absorbance at 254 nanometers (UV-254) in water in water from 20 community water-supply wells in New Jersey, from 20 community water-supply wells in New Jersey, 1998-99. 1998-99. THMs and HAAs in treated waters did not appear to be related anthropogenic, on the basis of the existing data, such inputs to concentrations of bromide, however, with the exception of cannot be separated from naturally occurring organic carbon CHBr3. The concentrations of CHBr3 were higher in treated which, in some cases, is known to be substantial. In the case of water from most of the wells in the bedrock aquifers than water in the confined aquifers, all of the organic carbon in the in treated water from most of the wells in the other aquifers water is derived from natural sources, because anthropogenic (table 9). Source waters from the bedrock aquifers generally inputs to unconfined parts of the aquifers have had insufficient were as rich or richer in bromide as source water to wells in time to travel far downgradient beneath the overlying confin- the other aquifers (fig. 20). Concentrations of the other bro- ing units. 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 Bromide concentration is not the sole factor in formation of some of the brominated DBPs. Nevertheless, where concentrations of Concentrations of bromide in source water to the 20 wells bromide either are high naturally, or are enhanced by anthro- varied substantially (fig. 20). In some cases, high concentra- pogenic inputs (as in water from well 030301), concentrations tions (greater than 0.1 mg/L) likely were of anthropogenic of CHBr are likely to be high in treated water. origin—in particular, in water from well 030301, completed 3 in a bedrock aquifer, where concentrations of sodium and chloride were highly elevated (209 and 634 mg/L, respec- Iron, Manganese, and Ammonia tively). Concentrations of bromide in the confined aquifers, on the other hand, are natural. Concentrations of the brominated Miller and others (1990) found, in a study of organic carbon and THMFP in Kansas aquifers, that THMFP was strongly Differences in Disinfection By-Product Formation Potential in Water from Different Aquifer Types

0.20 1.6

0.15 1.2

0.10

0.8

2 0.05 R = 0.58 p-value = 0.010

CONCENTRATION OF BROMIDE, IN MILLIGRAMS PER LITER CONCENTRATION 0.4

0.00 DOC CONCENTRATION, IN MILLIGRAMS PER LITER

270080270147270155270182390451050039070177070368150207230195291264010039010600090136150276030301030460130098210402 350083 WELL NUMBER

0.0 EXPLANATION 0.0 0.4 0.8 1.2 1.6

AQUIFER TYPE AMMONIA CONCENTRATION, IN MILLIGRAMS PER LITER AS N Glacial Confined Coastal Plain EXPLANATION Unconfined Coastal Bedrock AQUIFER TYPE Plain Unconfined Coastal Confined Coastal Figure 20. Concentrations of bromide in water from 20 Plain Plain community water-supply wells in New Jersey, by aquifer type, Figure 21. Relation of concentrations of dissolved organic 1998-99. carbon (DOC) to concentrations of ammonia in water from 20 community water-supply wells in New Jersey Coastal Plain related to ground-water concentrations of TOC, which, in turn, aquifers, 1998-99. were related to concentrations of iron, manganese, and ammonia. Causes suggested for these relations include (1) reducing nia, whereas essentially none of the ammonia + organic nitro- conditions under which less TOC was microbially metabo- gen measured in water samples from the bedrock and glacial lized, (2) presence of colloids with which TOC and the other aquifers was ammonia. The relation between organic carbon three constituents are associated, and (3) complexation of iron and ammonia in water from the Coastal Plain aquifers may be, and manganese by organic matter. In this study, concentrations in part, a result of the character of the organic carbon pres- of iron and manganese, which likely are derived mostly from ent in the ground water. In particular, in the confined Coastal minerals in the aquifers, varied by three orders of magnitude. Plain aquifers, the ammonia probably derives mostly from The higher concentrations of iron and manganese typically the microbial decomposition of organic matter in the aquifers. occurred in water with low oxygen content. Concentrations of Brown coal (lignite), for example, can contain more than 5 iron and manganese were not related to concentrations of TOC weight-percent of nitrogen (Muller-Wegener, 1988); lignite or DOC. Because the concentrations of iron and manganese is ubiquitous in sediments of the Potomac-Raritan-Magothy reported in this study are for filtered samples, whereas the aquifer system of the New Jersey Coastal Plain. Most of the samples in the study of Miller and others (1990) apparently water samples from the Coastal Plain aquifers had low oxygen were not filtered, comparisons of results are viewed with cau- content; therefore, any inputs of nitrogen to the ground water tion. Furthermore, in this study, ammonia was not detected in at the sampling points would be in a reduced form, such as any water samples from the bedrock or glacial aquifers. For ammonia. the water samples from the Coastal Plain aquifers, however, Reckow and others (1990) found a positive relation in which ammonia was detected, relations between concentra- 2 between organic N and production of Cl2AN. In this study, tions of ammonia and DOC were positive (r = 0.58) (fig. 21) concentrations of ammonia + organic nitrogen for all wells and similar to results from Miller and others (1990). showed only a weak positive relation with concentrations Nearly all of the ammonia + organic nitrogen measured 2 of total HANs (r = 0.17). Cl2AN developed in water from in water samples from the Coastal Plain aquifers was ammo- unconfined Coastal Plain wells, but there were insufficient Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 detections to draw any conclusions about relations with Water from all wells completed in unconfined aquifers concentrations of ammonia + organic nitrogen. Using data contained one or more VOCs, some at concentrations exceed- for all 20 wells, the reduced species (ammonia + organic N) ing maximum contaminant levels (MCL). High concentra- did not relate strongly to concentrations of THMs (r2 =0.10) tions of sodium, chloride, and sulfate were present in water either. The possibility that concentrations of the reduced samples from several wells completed in unconfined aquifers nitrogen species might be higher as the aromatic content of the at levels exceeding secondary maximum contaminant levels organic carbon increased was explored because the nitrogen in (SMCLs) of 50, 250, and 250 mg/L, respectively. Although the ammonia and amino compounds can become covalently linked high levels of sulfate were natural, the high concentrations of to various aromatic structures (Anderson and others, 1989). sodium and chloride were indicative of anthropogenic inputs Using the data for all 20 wells, the relation between UV-254 to ground water. measurements and ammonia + organic nitrogen was not strong Concentrations of nitrate exceeding 1 mg/L as N were (r2 = 0.16). It was only slightly stronger for water from the present in samples from most of the wells in bedrock and unconfined Coastal Plain wells (r2 = 0.31). Relations between glacial aquifers, although none exceeded the MCL of 10 mg/L SUVA and ammonia + organic nitrogen were weaker than as N. Because water from most of the Coastal Plain wells had those between UV-254 measurements and ammonia + organic low oxygen contents, no nitrate was detected in samples from nitrogen. 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 Indicators of Disinfection By-Product Formation contained detectable concentrations of ammonia, however. Potential Water from the 20 wells was chlorinated and incubated for 7 days. With few exceptions, higher concentrations of Overall, it appears that the aromatic character of the DBPs were formed in water from the wells in Coastal Plain organic matter is an important factor in DBP production in aquifers than in water from wells in bedrock or glacial aqui- the ground water sampled during this study. UV-254 measure- fers. A positive relation was observed between the formation ments likely could be used to predict the potential of ground potentials for the classes of DBPs and the aromaticity of the water to DBP formation upon chlorination because they would precursor DOC, as estimated by measurements of ultraviolet be indicative of both the magnitude of concentrations of DOC absorption at 254 nanometers. Water samples from seven and the aromaticity of the DOC. Chemical constituents other selected wells were chlorinated and incubated for 6, 24, and than DOC appear to be poor indicators of DBP formation 168 hours. Water from Coastal Plain wells, in general, devel- potential. Nevertheless, because the pHs of the treated water oped higher concentrations of THMs, HAAs, and HANs than samples in this study were adjusted to 7 before chlorination, did the samples from bedrock and glacial aquifers. Rates of relations between THMFP and various constituents may be formation were variable. different for waters chlorinated prior to pH adjustment. DOC in water samples was fractionated to determine The presence of ammonia in source water to the wells in hydrophobic and hydrophilic fractions. DOC in water from the Coastal Plain aquifers raises the issue of the effectiveness the wells in Coastal Plain aquifers contained, in some cases, of chlorination. Reactions between chlorine and ammonia slightly larger concentrations of hydrophobic organic acids result in compounds that are less effective as disinfectants, than did DOC in water from wells in the bedrock and glacial although this can be overcome by increases in the chlorine aquifers. When treated with chlorine, both the hydrophobic dose (McClanahan, 1977). and hydrophilic acid fractions developed DBPs. Concentra- tions of THMs and HAAs generally were higher in the hydrophobic fraction of DOC from Coastal Plain aquifers than in Summary and Conclusions the same fractions from bedrock and glacial aquifers. DOC in water from wells in unconfined aquifers may Water samples were collected from 20 community water- derive partly from the VOCs that are present, but concentra- supply wells in New Jersey, of which 16 were completed in tions of DOC in most of these water samples were typical of unconfined bedrock, glacial, and Coastal Plain aquifers, and DOC levels in the unconfined aquifers. Water from one well 4 were completed in confined Coastal Plain aquifers. The in a glacial aquifer contained several VOCs, some at concen- samples were analyzed for major and minor ions, selected trations exceeding MCLs, and the concentration of DOC was trace elements, total organic carbon (TOC), dissolved organic high relative to concentrations in samples from most other carbon (DOC), and volatile organic compounds (VOCs). DOC wells. Another well in an unconfined Coastal Plain aquifer fractions were determined. Raw water samples were chlo- yielded water with an equally high concentration of DOC, rinated, the pH adjusted to 7, and analyzed for the common but only one VOC was detected at a low concentration. The groups of disinfection by-products (DBPs): trihalomethanes sediments of the Coastal Plain aquifers contain substantial (THMs), haloacetic acids (HAAs), and haloacetonitriles amounts of organic matter that can contribute aromatic DOC (HANs) after incubation for 168 hours (7 days). Selected chlo- compounds to the ground water. Thus, much of the DOC in rinated samples also were incubated for 6 and 24 hours. water from the wells in unconfined Coastal Plain aquifers References Cited probably was natural. The DOC in water from the wells in the Ayers, M.A., and Pustay, E.A., 1988, New Jersey Ground- confined Coastal Plain aquifers was wholly natural in origin, water quality, in Moody, D.W., Carr, Jerry, Chase, E.B., and as the wells are too far downgradient beneath confining units Paulson, R.W., National Water Summary 1986; Hydrologic to receive anthropogenic inputs. events and ground-water quality: U.S. Geological Survey Organic material is present in some of the sedimentary Water-Supply Paper 2325, 506 p. rocks of the bedrock aquifers, but it may not be readily incor- porated into the ground water. Organic matter in the unconsol- Bloemen, H.J. Th., and Burn, J., eds. 1993, Chemistry and idated materials of the glacial aquifers probably occurs sporad- analyses of volatile organic compounds in the environment: ically. The geologic characteristics of the aquifers do appear Glasgow, Scotland, Blackie Academic and Professional, 290 to be an important factor in the supply of organic carbon to p. the ground water, and thus can play a role in the potential of Brenton, R.W., and Arnett, T.L., 1993, Methods of analysis by ground water to form DBPs when chlorinated. the U.S. Geological Survey National Water Quality Labora- tory—Determination of dissolved organic carbon by UV- promoted persulfate oxidation and infrared spectrometry: Acknowledgments U.S. Geological Survey Open-File Report 92-480, 12 p. Clawges, R.M., Oden, T.D., and Vowinkel, E.F., 1998, Water- The authors thank the water purveyors for allowing quality data for 90 community water-supply wells in New access to their wells and express appreciation to Judy Louis Jersey, 1994-95: U.S. Geological Survey Open-File Report of NJDEP for assistance with study design. Thanks are due 97-625, 31 p. also to USGS colleagues: George R. Aiken for his guidance in fractionation techniques, and Jacob Gibs and Gary K. Speiran Connor, B.F., Rose, D.L., Noriega, M.C., Murtagh, L.K., and for insightful comments that greatly improved the manuscript. Abney, S.R., 1998, Methods of analysis by the U. S. Geo- logical Survey National Water Quality Laboratory—Deter- mination of 86 volatile organic compounds in water by References Cited purge and trap capillary-column gas chromatography mass spectrometry, reporting results at low microgram-per-liter concentrations: U.S. Geological Survey Open-File Report Adin, A., Katzhendler, J., Alkaslassy, D., Rav-Acha, C., 1991, 97-829. Trihalomethane formation in chlorinated drinking water: a kinetic model: Water Research, v. 25, no. 7, p. 797-805 Eaton, A.D., Clesceri, L.S., and Greenberg, A.E., 1995, Stan- dard methods for the examination of water and wastewater Adriano, D.C., 1986, Trace elements in the terrestrial environ- (19th ed.): Washington, D.C., American Public Health ment: New York, Springer-Verlag, 533 p. Association, 949 p. Aiken, G.R., 1985 Isolation and concentration techniques for Fishman, M.J., and Friedman, L.C., 1989, Methods for aquatic humic substances, in Aiken, G.R., McKnight, D.M., determination of inorganic substances in water and fluvial Wershaw, R.L., and MacCarthy, P., eds., Humic substances sediments: U.S. Geological Survey Techniques of Water in soil, sediment, and water: New York, Wiley, p. 363-385. Resources Investigations, book 5, chap. A1, 545 p. Aiken, G.R., McKnight, D.M., Thorn, K.A., and Thurman, Friedman, L.C., and Erdmann, D.E., 1982, Quality assurance E.M., 1992, Isolation of hydrophilic organic acids from practices for the chemical and biological analyses of water water using nonionic macroporous resins: Organic Geo- and fluvial sediments: U.S. Geological Survey Techniques chemistry, v. 18, p. 567-573. of Water Resources Investigations, book 5, chap. A6, 181 p. Anderson, H.A., Bick, W., Hepburn, A, and Stewart, M., 1989, Graedel, T.E., and Reiss, N.M. 1985, Chapter I, Atmospheric Nitrogen in humic substances, in Hayes, M.H.B., Mac- Processes, in Panel on Acidic Deposition in New Jersey, ed., Carthy, P., Malcolm, R.L., and Swift, R.S., eds., Humic Acidic Deposition in New Jersey, A report to the Governor Substances II: Chichester, England, John Wiley and Sons and Legislature of New Jersey, The Governor’s Science Ltd., p. 223-253. Advisory Committee: On file at New Jersey Department of Environmental Protection, Trenton, New Jersey; p. 19-52. Andrews, R.C., and Ferguson, M.J., 1996, Minimizing disinfection by-product formation while ensuring Giardia Hem, J.D., 1992, Study and interpretation of the chemical control, in Minear, R.A., and Amy, G.L , eds., Disinfection characteristics of natural water: U.S. Geological Survey by-products in water treatment, the chemistry of their for- Water-Supply Paper 2254, 264 p. mation and control: New York, Lewis Publishers, p. 17-58. 38 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Hoekstra, E.J., De Leer, E.W.B., and Brinkman, U.A. Th., Muller-Wegener, U., 1988, Interaction of humic substances 1998, Natural formation of chloroform and brominated tri- with biota, in Frimmel, F.H., and Christman, R.F., eds., halomethanes in soil: Environmental Science and Technol- Humic substances and their role in the environment: Chich- ogy, v. 32, p. 3724-3729. ester, England, John Wiley and Sons, p. 179-192. Koterba, M.T., Wilde, F.D., and Lapham, W.W., 1995, New Jersey Department of Environmental Protection, 1997, Ground-water data-collection protocols and procedures for Standards for safe drinking water in New Jersey: Trenton, the National Water-Quality Assessment Program: Collection N. J., New Jersey Department of Environmental Protection, and documentation of water-quality samples and related November 1997. data: U.S. Geological Survey Open-File Report 95-399, 113 p. Owens, J.P., and Sohl, N.F., 1969, Shelf and deltaic paleoenvi- ronments in the Cretaceous-Tertiary formations of the New Kretzschmar, Ruben, Robarge, W.P., and Amoozegar, Aziz., Jersey Coastal Plain, in Subitsky, Seymour, ed., Geology of 1995, Influence of natural organic matter on colloid trans- selected areas in New Jersey and eastern Pennsylvania and port through saprolite: Water Resources Research, v. 31, guidebook of excursions: New Brunswick, N.J., Rutgers p. 435-445. University Press, p. 235-278. Larson, R.A., and Weber, E.J., 1994, Reaction mechanisms in Perlmutter, N.M., and Koch, E., 1972, Preliminary hydro- environmental organic chemistry: Boca Raton, Fla., Lewis geologic appraisal of nitrate in ground water and streams, Publishers, 433 p. southern Nassau County, Long Island, New York: U.S. Geological Survey Professional Paper 800-B, p. 225-235. Liang, Lin, and Singer, P.C., 2003, Factors influencing the formation and relative distribution of haloacetic acids and Pomes, M.L., Larive, C.K., Thurman, E.M., Green, W.R., trihalomethanes in drinking water: Environmental Science Orem, W.H., Rostad, C.E., Coplen, T.B., Cutak, B.J., and and Technology, v. 37, p. 2920-2928. Dixon, A.M., 2000, Sources and haloacetic acid/trihalomethane formation potentials of aquatic humic substances Louis, J.B., Sanders, P.F., and Bono, P.M., 1994, Implementa- in the Wakarusa River and Clinton Lake near Lawrence, tion of a program to assess the vulnerability of New Jersey’s Kansas: Environmental Science and Technology, v. 34, drinking water supplies to pesticide contamination, in Weig- p. 4278-4286. mann, D.L, ed., Proceedings of the Fourth National Confer- ence on Pesticides, November 1-3, 1993—New Directions Pritt, J.W. and Raese, J.W., 1995, Quality assurance/qual- in pesticide research, management, and policy: Blacksburg, ity control manual—National Water Quality Laboratory: Va., Virginia Resources Research Center, p. 167-183. U.S.Geological Survey Open-File Report 95-443, 35 p. Madison, R.J. and Brunett, J.O., 1985, Overview of the occur- Reckow, D.A., Singer, P.C., and Malcolm, R.L., 1990, Chlori- rence of nitrate in ground water of the United States, in nation of humic materials: Byproduct formation and chemi- National Water Summary 1984; hydrologic events, selected cal interpretations: Environmental Science and Technology, water-quality trends, and ground-water resources: U.S. Geo- v. 24, p. 1655-1664. logical Survey Water-Supply Paper 2275, p. 93-105. Rook, J.J., 1974, Formation of haloforms during chlorination McCarthy, J.F., and Zachara, J.M., 1989, Subsurface transport of natural water: Water Treatment Examiner, v. 23, p. 234- of contaminants: Environmental Science and Technology, 243. v. 23, p. 496-502. Smith, J.A., Witkowski, P.J., and Fusillo, T.V., 1988, Man- McClanahan, M.A., 1977, Recycle—what disinfectant for safe made organic compounds in the surface waters of the water then?, in Johnson, J.D., ed., Disinfection, water and United States—a review of current understanding: U.S. wastewater: Ann Arbor, Mich., Ann Arbor Science Publish- Geological Survey Circular 1007, 92 p. ers, Inc., p. 49-65. Stackelberg, P.E., Hopple, J.A., and Kauffman, L.J., 1997, Miller, R.E., Randtke, S.J., Hathaway, L.R., and Denne, J.E., Occurrence of nitrate, pesticides, and volatile organic com- 1990, Organic carbon and THM formation potential in Kan- pounds in the Kirkwood-Cohansey aquifer system, South- sas groundwaters: Journal of the AWWA, v. 82, p. 49-62. ern New Jersey: U.S. Geological Survey Water-Resources Investigations Report 97-4241. Minard, J.P., and Rhodehamel, E.C., 1969, Quaternary geology in part of northern New Jersey and the Trenton area, in Stevens, A.A., Slocum, C.J., Seeger, D.P., and Roebeck, G.G., Subitsky, Seymour, ed., Geology of selected areas in New 1976, Chlorination of organics in drinking water: Journal of Jersey and eastern Pennsylvania and guidebook of excur- the American Water Works Association, v. 68, p. 615. sions: New Brunswick, N. J., Rutgers University Press, p. 279-313. References Cited 9

Szabo, Zoltan, Zapecza, O.S., and Nawyn, J.P., 1989, Effects of ground-water chemistry on the distribution of dissolved uranium and radium-226 in the Newark Basin, New Jersey, in Daniel, C.C., III, White, R.K., and Stone, P.A., eds., Ground water in the Piedmont: Proceedings of a confer- ence on ground water in the Piedmont of the Eastern United States: Clemson, S. C., Clemson University Press, p. 566- 586. Thurman, E.M., 1985, Organic geochemistry of natural waters: Dordrecht, Holland, Martinus Nijhoff/Dr W. Junk Publishers., 497 p. U.S. Environmental Protection Agency, 1994, National primary drinking water regulations: monitoring requirements for public drinking water supplies: Cryptosporidium, Giardia, viruses, disinfection by-products, water treatment plant data and other information requirements; proposed rule: Federal Register 59 (28), 6332. U.S. Environmental Protection Agency, 1998, National Primary Drinking Water regulations: Disinfectants and disinfection byproducts, Final rule: Federal Register 63 (241) Wed. Dec. 16, 69413. U.S. Environmental Protection Agency, 2001, National Pri- mary Drinking Water Standards: Office of Water, Washing- ton, D.C., EPA 816-F-01-007, March 2001. Van Houten, F.B., 1969, Late Triassic Newark Group, north- central New Jersey and adjacent New York and Pennsylva- nia, in Subitsky, Seymour, ed., Geology of selected areas in New Jersey and eastern Pennsylvania and guidebook of excursions: New Brunswick, N. J., Rutgers University Press, p. 314-347. Verschueren, K., 1983, Handbook of environmental data on organic chemicals: New York, N.Y., Van Nostrand Reinhold Company, Inc., 1310 p. Wong, S., Hanna, J.V., King, S., Carroll, T.J., Eldridge, R.J., Dixon, D.R., Bolto, B.A., Hesse, S., Abbt-Braun, G., and Frimmel, F.H., 2002, Fractionation of natural organic matter in drinking water and characterization of 13C cross-polar- ization magic-angle spinning NMR spectroscopy and size exclusion chromatography: Environmental Science and Technology, v. 36, p. 3497-3503. Zapecza, O.S., 1989, Hydrogeologic framework of the New Jersey Coastal Plain, Regional Aquifer-System Analysis— northern Atlantic Coastal Plain: U.S. Geological Survey Professional Paper 1404-B, 49 p., 24 pl. 40 Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 Appendixes Appendix 1-1 Quality-assurance data (blanks, replicates, and related environmental samples) for water samples from community water-supply wells, New Jersey, 1998-99.

[BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; ANC, acid-neutralizing capacity; Lab, laboratory; µS/cm, microsiemens per centimeter at 25o Celsius; mg/L, milligrams per liter; µg/L, micrograms per liter; nd, no data; <, less than; E, estimated; M, presence verified but not quantified. 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.] Lab Lab specific Dissolved Total USGS Station ANC conduc- organic organic Calcium Magnesium Sodium Potassium Aquifer Date Lab pH well identification Sample type (mg/L as tance carbon carbon (mg/L) (mg/L) (mg/L) (mg/L) type sampled (00403) number number CaCO3) (µS/cm) (mg/L) (mg/L) (00915) (00925) (00930) (00935) (90410) (90095) (00681) (00680) 210402 BR 09/15/99 401936074393005 Environmental 218 6.9 571 1.0 1.0 68.2 23.0 15.9 1.67 210402 BR 09/15/99 401936074393005 Replicate 219 6.9 573 1 1 68 23.0 15.7 1.70 270155 GL 09/16/99 405018074274501 Environmental 157 7.3 710 0.6 0.6 73.8 26.3 21.9 1.39 270155 GL 09/16/99 405018074274501 Replicate 157 7.3 719 0.7 0.8 73.9 26.3 22.1 1.42 070177 CP 07/24/98 395521075043501 Environmental 45 6.3 344 0.7 1.0 36.0 8.52 9.55 5.62 070177 CP 07/24/98 395521075043501 Replicate 45 6.2 342 0.7 0.7 36.1 8.52 9.47 5.46

010039 CCP 07/30/98 392324074231401 Environmental 53 7.3 149 0.4 0.6 5.40 1.84 20.5 3.01 010039 CCP 07/30/98 392324074231401 Replicate 53 7.3 147 0.4 0.5 5.45 1.85 20.7 3.05 350083 BR 10/12/99 403557074275503 Blank 2 8.3 E2 <0.33 <0.3 <0.02 <0.014 <0.09 <0.24 230195 CP 07/21/98 402537074200201 Blank 2 6.8 2 0.2 0.2 <0.02 <0.004 <0.10 <0.1 210402 BR 09/14/99 401936074393005 Blank 2 7.8 2 <0.1 <0.3 <0.02 <0.120 <0.09 <0.1 090136 CCP 08/27/98 391152074392701 Blank 2 7.9 2 <0.01 <0.1 <0.02 <0.004 <0.10 <0.1 Appendixes 1

Appendix 1-1 Quality-assurance data (blanks, replicates, and related environmental samples) for water samples from community water-supply wells, New Jersey, 1998-99.—

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

Ammonia Nitrite + Ortho- Hardness USGS Ammonia + organic Iron Manganese Sulfate Chloride Fluoride Bromide Nitrite Silica nitrate phosphate (mg/L as well (mg/L as N) nitrogen (µg/L) (µg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L as N) (mg/L) (mg/L as N) (mg/L as P) CaCO ) number (00608) (mg/L as N) (01046) (01056) (00945) (00940) (00950) (71870) (00613) (00955) 3 (00631) (00671) (00900) (00623) 210402 <0.02 E0.08 <10 <2.2 22.3 40.7 <0.1 0.08 <0.01 1.04 0.05 24.5 270 210402 <0.02 E0.07 <10 <2.2 22.4 40.5 <0.1 0.08 <0.01 1.07 0.04 24.3 260 270155 <0.02 E0.07 E8 3.6 22.9 113 <0.1 0.05 <0.01 2.34 0.02 27.3 290 270155 <0.02 E0.06 E6 3.6 22.8 112 <0.1 0.06 <0.01 2.35 0.02 27.1 290 070177 0.20 0.18 6,970 242 59.5 29.1 <0.1 0.12 <0.01 0.05 0.06 13.1 130 070177 0.2 0.19 6,970 243 59.3 28.7 <0.1 0.13 <0.01 0.05 0.05 12.9 130

010039 0.15 0.16 72 20.1 11.6 3.42 0.2 0.02 <0.01 <0.05 0.29 32.6 21 010039 0.16 0.16 74 20.6 11.8 3.46 0.2 0.03 <0.01 <0.05 0.28 32.8 21 350083 <0.02 <0.10 <10 <2.2 <0.3 <0.29 <0.1 <0.01 <0.01 <0.05 <0.01 <0.1 nd 230195 0.02 <0.10 <10 <4.0 <0.1 <.01 <0.1 <0.01 <0.01 <0.05 0.01 <0.1 nd 210402 <0.02 <0.10 <10 <2.2 <0.3 <0.29 <0.1 <0.01 <0.01 <0.05 <0.01 0.3 nd 090136 <0.02 <0.10 <10 <4.0 <0.1 <0.1 <0.1 <0.01 <0.01 <0.05 <0.01 0.1 nd Appendix 1-1 Quality-assurance data (blanks, replicates, and related environmental samples) for water samples from community water-supply wells, New Jersey, 1998-99.— Continued Bromo- Carbon Dibromo- 1,2- 1,3- 1,4- Dichloro- 1,1- Dissolved Bromo- Chloro- USGS Benzene dichloro- tetra- Chloroform chloro- Dichloro- Dichloro- Dichloro- difluoro- Dichloro- solids form benzene well (µg/L) methane chloride (µg/L) methane benzene benzene benzene methane ethane (mg/L) (µg/L) (µg/L) number (34030) (µg/L) (µg/L) (32106) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (70301) (32104) (34301) (32101) (32102) (32105) (34536) (34566) (34571) (34668) (34496) 210402 325 <0.10 <0.05 <0.10 <0.09 <0.03 E0.05 <0.2 <0.05 <0.05 <0.05 <0.14 <0.07 210402 331 <0.10 <0.05 <0.10 <0.09 <0.03 E0.05 <0.2 <0.05 <0.05 <0.05 <0.14 <0.07 270155 387 <0.04 E0.04 <0.06 <0.06 <0.03 4.10 <0.2 <0.05 <0.05 <0.05 <0.27 E0.05 270155 391 <0.04 E0.03 <0.06 <0.06 <0.03 3.98 <0.2 <0.05 <0.05 <0.05 <0.27 E0.05 070177 204 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 070177 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

010039 109 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 010039 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 350083 nd <0.04 <0.05 <0.06 <0.06 <0.03 <0.05 <0.2 <0.05 <0.05 <0.05 <0.27 <0.07 230195 nd <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 210402 nd <0.10 <0.05 <0.10 <0.09 <0.03 <0.05 <0.2 <0.05 <0.05 <0.05 <0.14 <0.07 090136 nd <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

Appendix 1-1 Quality-assurance data (blanks, replicates, and related environmental samples) for water samples from community water-supply wells, New

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

1,2- 1,1- cis-1,2- trans-1,2- 1,2- Methyl 1,1,1-Tri- Ethyl- Methylene Tetrachlro- Trichloro- USGS Dichloro- Dichloro- Dichloro- Dichloro- Dichloro- tert-butyl Styrene Toluene chlorobenzene chloride ethylene ethylene well ethane ethylene ethylene ethylene propane ether (µg/L) (µg/L) ethane (µg/L) (µg/L) (µgL) (µg/L) number (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (77128) (34010) (µg/L) (34371) (34423) (34475) (39180) (32103) (34501) (77093) (34546) (34541) (78032) (34506) 210402 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 M <0.04 <0.10 <0.05 <0.03 <0.04 210402 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 M <0.04 <0.10 <0.05 <0.03 <0.04 270155 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 0.7 <0.04 <0.10 <0.05 0.25 <0.04 270155 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 0.7 <0.04 <0.10 <0.05 0.26 <0.04 070177 2.9 <0.2 10.0 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 1.9 <0.2 <0.2 43.0 070177 3 <0.2 10.4 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 2 <0.2 <0.2 40.0 010039 <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 010039 <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 350083 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 <0.2 <0.04 <0.10 E0.08 <0.03 <0.04 230195 <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 210402 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 <0.2 <0.04 <0.10 E0.02 <0.03 <0.04 090136 <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

Appendix 1-1 Quality-assurance data (blanks, replicates, and related environmental samples) for water samples from community water-supply wells, New Jersey, 1998-99.—Continued

Trichloro- Vinyl m, p- fluoro- o-Xylene Xylene USGS well chloride Xylene methane (µg/L) (µg/L) number (µg/L) (µg/L) (µg/L) (77135) (81551) (39175) (85795) (34488) 210402 <0.09 <0.1 <0.06 <0.06 nd 210402 <0.09 <0.1 <0.06 <0.06 nd 270155 0.18 <0.1 <0.06 <0.04 nd 270155 0.18 <0.1 <0.06 <0.04 nd 070177 <0.2 <0.2 nd nd <0.2 070177 <0.2 <0.2 nd nd <0.2 010039 <0.2 <0.2 nd nd <0.2 010039 <0.2 <0.2 nd nd <0.2 350083 <0.09 <0.1 <0.06 <0.04 nd 230195 <0.2 <0.2 nd nd <0.2 210402 <0.09 <0.1 <0.06 <0.06 nd 090136 <0.2 <0.2 nd nd <0.2 Appendix 1-2 Quality-assurance data (blanks, replicates, and related environmental samples) for chlorinated water samples from community water-supply wells, New Jersey, 1998-99.

[BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; mg/L, milligrams per liter; µg/L, micrograms per liter; nd, no data; <, 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.] Bromo- Dibromo- Bromo- Incu- Chlorine Chlorine Bromo- Chloro- Chloral USGS Chlorate dichloro- chloro- chloro- Aquifer Date Time bation dose residual form form hydrate well Sample type (mg/L) methane methane acetic type collected collected time (mg/L) (mg/L) (µg/L) (µg/L) (µg/L) number (99320) (µg/L) (µg/L) acid (µg/L) (hours) (99300) (99301) (99307) (99304) (99321) (99305) (99306) (99322) 210402 BR 09/15/99 900 Environmental 168 5 5 1,800 6.7 3.7 4.9 6.3 1.5 3.2 210402 BR 09/15/99 901 Replicate 168 5 5 1,800 6.4 4 4.6 6.2 1.7 3.3 270155 GL 09/16/99 900 Environmental 168 5 4 1,800 5.8 2.5 7.5 5.4 1.8 2.3 270155 GL 09/16/99 901 Replicate 168 5 5 1,900 5 2.4 6.9 4.9 1.3 1.7 070177 CP 07/24/98 900 Environmental 168 10 4 1,600 15 1 17 7.1 2.7 3.1 070177 CP 07/24/98 901 Replicate 168 10 4 1,700 14 1 16 6.9 2.3 4.1

010039 CCP 07/28/98 900 Environmental 168 nd nd 850 8.6 0.2 31 3.2 <0.1 3.4 010039 CCP 07/28/98 901 Replicate 168 7.5 4 790 8.8 0.2 32 3.4 <0.1 3.2 350083 BR 10/12/99 1005 Blank 168 5 4 2,000 <0.1 <0.1 3 <0.1 3.7 <0.1 230195 CP 07/21/98 1005 Blank 168 7.5 6 95 <0.1 <0.1 6.8 <0.1 120 1.1 210402 BR 09/14/99 905 Blank 168 5 4 2,100 0.8 <0.1 4.8 0.1 5.8 <0.1 090136 CCP 08/27/98 1005 Blank 168 7.5 4 590 <0.1 <0.1 0.7 <0.1 1.2 <0.1 Appendixes

Appendix 1-2 Quality-assurance data (blanks, replicates, and related environmental samples) for chlorinated water samples from community water-supply wells, New Jersey, 1998-99.—Continued Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

Dibromo- Dichloro- Mono- Trichloro- Dichloro- Bromo- Dibromo- Trichloro- 1,1,1- 1,1- Chloro- USGS acetic acetic chloro- acetic aceto- chloro- aceto- aceto- Trichloro-2- Dichloro-2- Aquifer picrin well acid acid acetic acid nitrile acetonitrile nitrile nitrile propanone propanone type (µg/L) number (µg/L) (µg/L) acid (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (99319) (99312) (99309) (99308) (99310) (99314) (99315) (99316) (99313) (99317) (99318) 210402 BR 3.7 3.2 3.8 1.7 <0.1 0.6 1.0 <0.1 nd nd nd 210402 BR 4.1 3 <0.1 1.8 <0.1 0.6 1.1 <0.1 nd nd nd 270155 GL 2.5 2.1 2.8 1.7 <0.1 0.6 0.9 <0.1 nd nd nd 270155 GL 1.9 1.2 <0.1 1.2 <0.1 0.6 <0.1 <0.1 nd nd nd 070177 CP 1.4 6.9 <0.1 4.0 <0.1 <0.1 1.1 <0.1 nd nd nd 070177 CP 2 9.2 <0.1 5.4 <0.1 <0.1 1 <0.1 nd nd nd

010039 CCP <0.1 14 <0.1 18.0 <0.1 <0.1 <0.1 <0.1 nd nd nd 010039 CCP <0.1 14 <0.1 16 <0.1 <0.1 <0.1 <0.1 nd nd nd 350083 BR <0.1 1.9 <0.1 3.3 <0.1 <0.1 <0.1 <0.1 nd nd nd 230195 CP <0.1 3 <0.1 1.8 <0.1 <0.1 <0.1 <0.1 nd nd nd 210402 BR <0.1 2.9 4.1 3.4 <0.1 <0.1 <0.1 <0.1 nd nd 0.5 090136 CCP <0.1 <0.1 <0.1 <0.1 <0.1 <0.1 <0.1 <0.1 nd nd nd Appendix 2 Constituent concentrations in, and characteristics of, water samples from 20 community water-supply wells, New Jersey 1998-99.

[BRCKS, Brunswick; PSSC, Passaic; SCKN, Stockton; SFDF, Stratified Drift; MRPAU, Upper Potomac-Raritan-Magothy; MRPAM, Middle Potomac-Raritan-Magothy; MRPAL, Lower Potomac-Raritan-Magothy; ODBG, Oldbridge; CKKD, Kirkwood-Cohansey; KRKDL, Lower Kirkwood; BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; Lab, laboratory; ANC, acid-neutralizing capacity; µS/cm, microsiemens per centimeter at 25o Celsius; oC, degrees Celsius; mg/L, milligrams per liter; µg/L, micrograms per liter, nd, no data; <, less than; E, estimated; M, presence verified but not quantified. 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.] Lab Field alka- Lab Specific Dissolved Total Dissolved specific Temper- USGS linity ANC Field Lab conduc- organic organic Aquifer Aquifer Date Station identifi- oxygen conduc- ature well (mg/L as (mg/L as pH pH tance carbon carbon code type sampled cation number (mg/L) tance (oC) number CaCO ) CaCO ) (00400) (00403) (µS/cm) (mg/L) (mg/L) 3 3 (00300) (µS/cm) (00100) (39086) (90410) (00095) (00681) (00680) (90095) 030301 227BRCKS BR 09/22/99 410046074074701 160 166 1.8 7.7 7.5 2,250 2,260 12.5 0.2 0.4 030460 227PSSC BR 09/22/99 405540074081601 189 200 5.3 7.3 7.1 697 697 14.5 0.9 0.3 130098 227PSSC BR 09/21/99 404534074140201 181 195 3.4 7.3 7.2 956 943 13.4 0.9 0.5 210402 231SCKN BR 09/15/99 401936074393005 206 218 3.0 6.8 6.9 575 571 13.9 1.0 1.0 350083 227PSSC BR 10/07/99 403557074275503 131 133 1.2 7.4 7.4 1,450 1,430 12.9 0.6 0.5

270080 112SFDF GL 09/20/99 405414074310901 145 155 2.1 7.8 7.5 589 594 11.9 0.7 0.5 270147 112SFDF GL 09/20/99 404856074233901 196 206 0.1 7.9 7.8 685 686 12.4 1.4 1.2 270155 112SFDF GL 09/16/99 405018074274501 149 157 0.6 7.3 7.3 713 710 14.1 0.6 0.6 270182 112SFDF GL 09/21/99 405111074231001 134 138 1.3 8.1 7.8 382 390 12.1 0.4 E0.2 390451 112SFDF GL 09/23/99 404248074185202 174 185 3.3 7.4 7.4 663 654 12.9 0.8 0.4

050039 211MRPAM CP 07/28/98 400404074552001 37 38 3.1 5.7 6.1 275 280 13.4 0.5 0.7 070177 211MRPAL CP 07/24/98 395521075043501 58 45 0.1 5.9 6.3 347 344 14.0 0.7 1.0 070368 211MRPAL CP 07/27/98 395848075034701 71 61 0.1 6.5 6.7 255 245 15.2 1.1 1.0 150207 211MRPAL CP 07/29/98 395156075105301 146 145 0.1 6.4 6.7 399 385 13.4 1.4 1.4 230195 211ODBG CP 07/22/98 402537074200201 <1 <1 0.1 4.8 5.1 258 259 14.6 1.0 1.2 291264 121CKKD CP 07/23/98 400500074045501 <1 4 2.5 4.7 5.0 184 185 13.2 0.8 0.9

010039 122KRKDL CCP 07/28/98 392324074231401 49 53 0.1 6.7 7.3 143 149 18.2 0.4 0.6 010600 122KRKDL CCP 07/30/98 392045074284001 45 54 0.1 7.0 7.7 142 149 18.6 0.4 0.6 090136 122KRKDL CCP 07/31/98 391152074392701 83 78 0.1 7.7 8.1 203 212 18.8 0.5 0.5 150276 211MRPAU CCP 07/27/98 394821075102601 128 128 0.1 7.7 8.1 382 379 14.4 0.7 0.8 Appendixes 4 8

Appendix 2 Constituent concentrations in, and characteristics of, water samples from 20 community water-supply wells, New Jersey 1998-99.—Continued Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 Bromodi- Carbon Dibromo- Hardness Dissolved Bromo- Chloro- 1,2-Dichlo- 1,3-Dichlo- 1,4-Dichlo- USGS Silica Benzene chloro- tetra- Chloroform chloro- (mg/L as solids form benzene robenzene robenzene robenzene well (mg/L) (µg/L) methane chloride (µg/L) methane CaCO ) (mg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) number (00955) 3 (34030) (µg/L) (µg/L) (32106) (µg/L) (00900) (70301) (32104) (34301) (34536) (34566) (34571) (32101) (32102) (32105) 030301 15.8 540 1,180 <0.04 <0.05 <0.06 <0.06 <0.03 0.24 <0.2 <0.05 <0.05 <0.05 030460 18.9 270 396 E0.01 E0.04 <0.06 E2.27 <0.03 2.41 <0.2 <0.05 <0.05 <0.05 130098 23.9 370 531 <0.04 <0.05 <0.06 0.33 <0.03 0.93 <0.2 <0.05 <0.05 <0.05 210402 24.5 270 325 <0.1 <0.05 <0.1 <0.09 <0.03 E0.05 <0.2 <0.05 <0.05 <0.05 350083 19.6 770 1,110 <0.04 <0.05 <0.06 <0.06 <0.03 0.26 <0.2 <0.05 <0.05 <0.05 270080 24.7 230 324 <0.04 <0.05 <0.06 <0.06 <0.03 E0.08 <0.2 <0.05 <0.05 <0.05 270147 25.5 280 394 <0.04 <0.05 <0.06 <0.06 <0.03 E0.07 <0.2 <0.05 <0.05 <0.05 270155 27.3 290 387 <0.04 E0.04 <0.06 <0.06 <0.03 4.10 <0.2 <0.05 <0.05 <0.05 270182 21.9 180 228 <0.04 <0.05 <0.06 E0.03 <0.03 E0.05 <0.2 <0.05 <0.05 <0.05 390451 24.5 280 378 <0.04 <0.05 <0.06 <0.06 <0.03 0.44 <0.2 <0.05 <0.05 <0.05 050039 10.0 78 150 <0.2 0.5 <0.2 <0.2 <0.2 37.9 <0.2 <0.2 <0.2 <0.2 070177 13.1 130 204 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 070368 6.4 65 138 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 150207 13.0 84 219 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 230195 6.1 38 nd <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 291264 5.6 33 101 0.5 <0.2 <0.2 <0.2 <0.2 0.8 <0.2 0.3 0.3 0.3 010039 32.6 21 109 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 010600 31.3 23 105 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 090136 19.9 31 136 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 150276 8.7 33 216 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 Appendix 2 Constituent concentrations in, and characteristics of, water samples from 20 community water-supply wells, New Jersey 1998-99.—Continued

trans- Methyl Dichloro- 1,1- 1,2- 1,1- cis-1,2- 1,2- 1,2- Ethyl- Methylene tert Tetrachloro- USGS difluoro- Dichloro- Dichloro- Dichloro- Dichloro- Dichloro- Styrene Toluene Dichloro- benzene chloride butyl ethylene well methane ethane ethane ethylene ethylene propane (µg/L) (µg/L) ethylene (µg/L) (µg/L) ether (µg/L) number (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (77128) (34010) (µg/L) (34371) (34423) (µg/L) (34475) (34668) (34496) (32103) (34501) (77093) (34541) (34546) (78032) 030301 <0.27 0.27 <0.1 0.17 0.13 <0.03 <0.07 <0.03 <0.4 0.9 <0.04 4.00 <0.05 030460 <0.27 0.15 <0.1 0.15 E0.05 <0.03 <0.07 <0.03 <0.4 1.3 <0.04 23.0 <0.05 130098 E0.18 0.13 <0.1 E0.06 1.32 E0.01 <0.07 <0.03 <0.4 4.3 <0.04 19.4 <0.05 210402 <0.14 <0.07 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 M <0.04 <0.1 <0.05 350083 <0.27 0.14 <0.1 0.18 0.63 <0.03 <0.07 <0.03 <0.4 E0.1 <0.04 1.86 <0.05

270080 <0.27 1.06 <0.1 0.26 0.38 <0.03 <0.07 <0.03 <0.4 0.2 <0.04 E0.08 <0.05 270147 <0.27 0.79 <0.1 0.42 1.90 E0.02 <0.07 <0.03 <0.4 1.6 <0.04 E0.08 <0.05 270155 <0.27 E0.05 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 0.7 <0.04 <0.1 <0.05 270182 E0.03 <0.07 <0.1 E0.02 <0.04 <0.03 <0.07 <0.03 <0.4 E0.1 <0.04 <0.1 <0.05 390451 <0.27 <0.07 <0.1 <0.04 <0.04 <0.03 <0.07 <0.03 <0.4 E0.1 <0.04 0.26 <0.05

050039 <0.2 0.5 <0.2 <0.2 2.0 <0.2 <0.2 <0.2 <0.2 0.6 <0.2 <0.2 <0.2 070177 <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 070368 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 0.9 <0.2 <0.2 <0.2 150207 <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 230195 <0.2 <0.2 0.3 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2 <0.2

291264 <0.2 0.5 <0.2 <0.2 0.3 <0.2 <0.2 <0.2 <0.2 2.6 <0.2 <0.2 <0.2 010039 <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 010600 <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 090136 <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 150276 <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 5 0 Appendix 2 Constituent concentrations in, and characteristics of, water samples from 20 community water-supply wells, New Jersey 1998-99.—Continued Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99 Ammonia Nitrite + Potas- Mang- Ortho- USGS Calcium Magnesium Sodium Ammonia + organic Iron Sulfate Chloride Fluoride Bromide Nitrite nitrate sium anese phosphate well (mg/L) (mg/L) (mg/L) (mg/L as N) nitrogen (µg/L) (mg/L) (mg/L) (mg/L) (mg/L) (mg/L as N) (mg/L (mg/L) (µg/L) (mg/L as P) number (00915) (00925) (00930) (00608) (mg/L as N) (01046) (00945) (00940) (00950) (71870) (00613) as N) (00935) (01056) (00671) (00623) (00631) 030301 115 61.6 209 2.01 <0.02 <0.10 <10 E 1.8 31.5 634 <0.1 0.19 <0.010 2.47 0.01 030460 79.2 17.7 28.8 3.87 <0.02 E0.07 <10 E 2.1 32.1 74.0 <0.1 0.06 <0.010 4.86 0.01 130098 121 17.1 36.8 1.55 <0.02 <0.10 <10 <2.2 55.7 150 <0.1 0.18 <0.010 3.63 0.03 210402 68.2 23.0 15.9 1.67 <0.02 E0.08 <10 <2.2 22.3 40.7 <0.1 0.08 <0.010 1.04 0.05 350083 271 22.7 39.2 1.54 <0.02 E0.09 <10 <2.2 623 36.7 0.2 0.10 <0.010 2.95 0.03

270080 52.8 23.7 25.2 1.82 <0.02 <0.10 <10 3.1 23.8 78.5 <0.1 0.05 <0.01 1.49 0.03 270147 68.0 26.5 29.8 1.34 <0.02 E0.06 E 6 390 59.4 64.5 <0.1 0.04 0.028 0.17 0.08 270155 73.8 26.3 21.9 1.39 <0.02 E0.07 E 8 3.6 22.9 113 <0.1 0.05 <0.010 2.34 0.02 270182 44.3 15.9 8.06 0.89 <0.02 <0.10 23 <2.2 20.6 27.6 <0.1 0.06 <0.010 0.73 0.10 390451 85.0 16.0 23.2 1.18 <0.02 E0.09 <10 <2.2 39.0 73.2 <0.1 0.09 <0.010 2.54 0.02

050039 14.7 9.93 16.9 3.65 0.36 0.35 <10 16.1 29.5 28.4 <0.1 0.04 <0.010 3.19 0.01 070177 36.0 8.52 9.55 5.62 0.20 0.18 6,970 242 59.5 29.1 <0.1 0.12 <0.010 0.05 0.06 070368 16.9 5.68 16.0 2.46 1.35 1.3 5,540 1,830 17.8 21.2 0.2 0.05 <0.010 0.12 0.02 150207 24.0 5.81 42.2 5.82 0.72 0.70 4,400 92.6 7.3 27.2 0.3 0.15 <0.010 <0.05 <0.01 230195 10.8 2.78 22.9 1.68 0.79 0.87 3,570 181 45.1 41.6 <0.1 nd <0.010 0.05 <0.01

291264 8.47 2.95 15.7 3.16 0.27 0.31 34 70.3 24.4 25.5 <0.1 nd <0.010 2.79 <0.01 010039 5.40 1.84 20.5 3.01 0.15 0.16 72 20.1 11.6 3.42 0.2 0.02 <0.010 <0.05 0.29 010600 6.82 1.38 19.9 2.76 0.14 0.15 53 9.3 10.3 3.87 0.1 0.03 <0.010 <0.05 0.29 090136 9.52 1.75 31.4 3.16 0.17 0.17 107 <4 10.1 9.64 0.2 0.04 <0.010 <0.05 0.26 150276 9.32 2.27 67.3 5.33 0.34 0.32 106 6.3 15.6 27.9 1.4 0.11 <0.010 <0.05 0.17 Appendixes 1

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

1,1,1-Tri- Trichloro- Trichloro- Vinyl m, p-Xy- USGS chloro- fluoro- o-Xylene Xylene ethylene chloride lene well ethane methane (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) number (µg/L) (µg/L) (77135) (81551) (39180) (39175) (85795) (34506) (34488) 030301 0.82 1.32 <0.09 <0.1 <0.06 <0.04 nd 030460 0.59 0.62 <0.09 <0.1 <0.06 <0.04 nd 130098 0.17 4.38 E0.09 <0.1 <0.06 <0.04 nd 210402 <0.03 <0.04 <0.09 <0.1 <0.06 <0.06 nd 350083 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 nd 270147 2.23 12.1 <0.09 <0.1 <0.06 <0.04 nd 270155 0.25 <0.04 0.18 <0.1 <0.06 <0.04 nd 270182 0.40 0.15 E0.03 <0.1 <0.06 <0.04 nd 390451 E0.09 E0.01 <0.09 <0.1 <0.06 <0.04 nd

050039 <0.2 0.6 <0.2 <0.2 nd nd <0.2 070177 <0.2 43.0 <0.2 <0.2 nd nd <0.2 070368 <0.2 <0.2 <0.2 <0.2 nd nd <0.2 150207 <0.2 <0.2 <0.2 <0.2 nd nd <0.2 230195 <0.2 <0.2 <0.2 <0.2 nd nd <0.2

291264 0.2 0.9 <0.2 <0.2 nd nd <0.2 010039 <0.2 <0.2 <0.2 <0.2 nd nd <0.2 010600 <0.2 <0.2 <0.2 <0.2 nd nd <0.2 090136 <0.2 <0.2 <0.2 <0.2 nd nd <0.2 150276 <0.2 <0.2 <0.2 <0.2 nd nd <0.2 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. Water-Quality, Organic Carbon, and Disinfection By-Product, Water-Supply Wells, New Jersey, 1998-99

[BR, bedrock; GL, glacial; CP, unconfined Coastal Plain; CCP, confined Coastal Plain; mg/L, milligrams per liter; µg/L, micrograms per liter; nd, no data; <, less than; CHBrCl2 bromodichloromethane; CHBr3, bromoform; CHCl3, chloroform; CHBr2Cl, dibromochloromethane; BrClAA, bromochloroacetic acid; Br2AA, dibromoacetic acid; Cl2AA dichloroacetic acid; ClAA, monochloroacetic acid; Cl3AA, trichloroacetic acid; BrClAN, bromochloroacetonitrile; Br2AN, dibromoacetonitrile; Cl2AN, dichloroacetonitrile; Cl3AN, trichloroacetonitrile. 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.]

Chlorine Chlorine USGS CHBrCl CHBr CHCl CHBr Cl BrClAA Br AA Cl AA ClAA Cl AA BrClAN Br AN Aquifer Incubation dose residual 2 3 3 2 2 2 3 2 well (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) (µg/L) type (hours) (mg/L) (mg/L) number (99305) (99307) (99304) (99306) (99322) (99312) (99309) (99308) (99310) (99315) (99316) (99300) (99301) 210402 BR 6 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 210402 BR 24 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 210402 BR 168 5.0 5.0 6.7 3.7 4.9 6.3 3.2 3.7 3.2 3.8 1.7 0.6 1.0 350083 BR 6 5.0 4.0 0.7 0.3 1.2 0.9 <0.1 <0.1 1.2 <0.1 1.2 <0.1 <0.1 350083 BR 24 5.0 4.0 1.3 0.5 1.5 1.5 <0.1 <0.1 1.1 <0.1 1.6 0.5 <0.1 350083 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

270155 GL 6 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 270155 GL 24 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 270155 GL 168 5.0 4.0 5.8 2.5 7.5 5.4 2.3 2.5 2.1 2.8 1.7 0.6 0.9 390451 GL 6 5.0 4.0 1.5 0.2 1.7 1.2 <0.1 <0.1 <0.1 <0.1 1.3 0.7 0.7 390451 GL 24 7.5 4.5 2.8 0.3 3.3 1.7 1.2 <0.1 1.1 <0.1 1.8 0.9 0.9 390451 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

230195 CP 6 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 230195 CP 24 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 230195 CP 168 1.0 0.5 29.0 2.2 35.0 17.0 8.5 4.1 15.0 2.3 13.0 3.0 3.1 150207 CP 6 10.0 2.1 8.4 1.7 7.5 7.5 3.1 2.6 3.3 <0.1 4.0 3.0 3.2 150207 CP 24 10.0 1.6 16.0 2.6 15.0 12.0 4.0 2.9 3.8 <0.1 4.7 3.9 4.7 150207 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

010600 CCP 6 nd nd 4.6 0.1 13.0 1.9 1.6 <0.1 4.9 <0.1 2.7 1.0 0.6 010600 CCP 24 nd nd 6.7 0.2 20.0 2.8 2.4 <0.1 6.4 <0.1 3.3 <0.1 <0.1 010600 CCP 168 nd nd 8.8 <0.1 30.0 2.3 2.5 <0.1 9.8 <0.1 4.0 <0.1 <0.1 Appendixes

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.—Continued

USGS CL AN CL AN Aquifer Incubation 2 3 well (µg/L) (µg/L) type (hours) number (99314) (99313) 210402 BR 6 <0.1 <0.1 210402 BR 24 0.6 <0.1 210402 BR 168 <0.1 <0.1 350083 BR 6 <0.1 <0.1 350083 BR 24 <0.1 <0.1 350083 BR 168 <0.1 <0.1

270155 GL 6 <0.1 <0.1 270155 GL 24 <0.1 <0.1 270155 GL 168 <0.1 <0.1 390451 GL 6 <0.1 <0.1 390451 GL 24 <0.1 <0.1 390451 GL 168 <0.1 <0.1

230195 CP 6 1.8 <0.1 230195 CP 24 2.1 <0.1 230195 CP 168 2.0 <0.1 150207 CP 6 1.4 <0.1 150207 CP 24 2.0 <0.1 150207 CP 168 1.2 <0.1

010600 CCP 6 1.0 <0.1 010600 CCP 24 <0.1 <0.1 010600 CCP 168 <0.1 <0.1 For additional information, write to: Director U.S. Geological Survey New Jersey Water Science Center Mountain View Office Park 810 Bear Tavern Rd., Suite 206 West Trenton, NJ 08628 or visit our Web site at: http://nj.usgs.gov/ Hopple, Jessica A., Barringer, Julia L. and Koleis, Janece—Water-Quality Constituents, Dissolved-Organic-Carbon Fractions, and Disinfection By-Product Formation in Water from Community Water-Supply Wells in New Jersey, 1998-99—Scientific Investigations Report 2006-5260 Printed on recycled paper