(;loo SURFACE-WATER-QUALITY ASSESSMENT OF THE UPPER 

/;J~.A, ILLINOIS RIVER BASIN IN ILLINOIS, INDIANA, AND 

fl(; 9:;-;~e'-fS' WISCONSIN: MAJOR AND TRACE ELEMENTS IN WATER, 

SEDIMENT, AND BIOTA, 1978-90 

JAN 2 3 1996 

INDIANA 

U.S. GEOLOGICAL SURVEY 

Water-Resources Investigations Report 95-4045 

NATIONAL WATER - QUALITY ASSESSMENT PROGRAM 
WATER-QUALITY ASSESSMENT OF THE UPPER ILLINOIS 

RIVER BASIN IN ILLINOIS, INDIANA, AND WISCONSIN: 

MAJOR AND TRACE ELEMENTS IN WATER, SEDIMENT, 

AND BIOTA, 1978-90 

by Faith A. Fitzpatrick, Barbara C. Scudder, J. Kent Crawford, Arthur R. Schmidt, 

Jennifer B. Sieverling, and others 

e U.S. GEOLOGICAL SURVEY 

Water-Resources Investigations Report 95--4045 

Iii 

1995 
U.S. DEPARTMENT OF THE INTERIOR 

BRUCE BABBITT, Secretary

U.S. GEOLOGICAL SURVEY 

Gordon P. Eaton, Director

For additional information Copies of this report can be

write to: purchased from:

District Chief U.S. Geological Survey

U.S. Geological Survey Information Services

102 E. Main St., 4th Floor Box 25286, Federal Center

Urbana, IL 61801 Denver, CO 80225
FOREWORD

The mission of the U.S. Geological Survey 

(USGS) is to assess the quantity and quality of the 

earth resources of the Nation and to provide information that will assist resource managers and policymakers at Federal, State, and local levels in making sound 

decisions. Assessment of water-quality conditions and 

trends is an important part of this overall mission.

One of the greatest challenges faced by waterresources scientists is acquiring reliable information 

that will guide the use and protection of the Nation's 

water resources. That challenge is being addressed by 

Federal, State, interstate, and local water-resource 

agencies and by many academic institutions. These 

organizations are collecting water-quality data for a 

host of purposes that include: compliance with permits 

and water-supply standards; development of remediation plans for specific contamination problems; operational decisions on industrial, wastewater, or watersupply facilities; and research on factors that affect 

water quality. An additional need for water-quality 

information is to provide a basis on which regionaland national-level policy decisions can be based. Wise 

decisions must be based on sound information. As a 

society we need to know whether certain types of 

water-quality problems are isolated or ubiquitous, 

whether there are significant differences in conditions 

among regions, whether the conditions are changing 

over time, and why these conditions change from 

place to place and over time. The information can be 

used to help determine the efficacy of existing waterquality policies and to help analysts determine the 

need for and likely consequences of new policies.

To address these needs, the U.S. Congress appropriated funds in 1986 for the USGS to begin a pilot program in seven project areas to develop and refine the 

National Water-Quality Assessment (NAWQA) Program. In 1991, the USGS began full implementation of 

the program. The NAWQA Program builds upon an 

existing base of water-quality studies of the USGS, as 

well as those of other Federal, State, and local agencies. 

The objectives of the NAWQA Program are to:

 Describe current water-quality conditions for a 

large part of the Nation's freshwater streams, 

rivers, and aquifers.

 Describe how water quality is changing over 

time.

 Improve understanding of the primary natural 

and human factors that affect water-quality 

conditions.

This information will help support the development 

and evaluation of management, regulatory, and monitoring decisions by other Federal, State, and local 

agencies to protect, use, and enhance water resources.

The goals of the NAWQA Program are being 

achieved through ongoing and proposed investigations 

of 60 of the Nation's most important river basins and 

aquifer systems, which are referred to as study units. 

These study units are distributed throughout the 

Nation and cover a diversity of hydrogeologic settings. 

More than two-thirds of the Nation's freshwater use 

occurs within the 60 study units and more than twothirds of the people served by public water-supply systems live within their boundaries.

National synthesis of data analysis, based on 

aggregation of comparable information obtained from 

the study units, is a major component of the program. 

This effort focuses on selected water-quality topics 

using nationally consistent information. Comparative 

studies will explain differences and similarities in 

observed water-quality conditions among study areas 

and will identify changes and trends and their causes. 

The first topics addressed by the national synthesis are 

pesticides, nutrients, volatile organic compounds, and 

aquatic biology. Discussions on these and other waterquality topics will be published in periodic summaries 

of the quality of the Nation's ground and surface water 

as the information becomes available.

This report is an element of the comprehensive 

body of information developed as part of the NAWQA 

Program. The program depends heavily on the advice, 

cooperation, and information from many Federal, 

State, interstate, Tribal, and local agencies and the 

public. The assistance and suggestions of all are 

greatly appreciated.

Robert M. Hirsch 

Chief Hydrologist
CONTENTS

Abstract .......................................................................................... 1

Introduction ....................................................................................... 1

Purpose and Scope............................................................................. 2

Acknowledgments ............................................................................. 4

Sources of Major and Trace Elements .............................................................. 4

Background Sources......................................................................4

Anthropogenic Sources ...................................................................5

Geochemistry of Major and Trace Elements ........................................................ 10

Fate and Effects of Major and Trace Elements on Aquatic Biota ........................................ 12

Criteria and Guidelines for Element Concentrations in Water, Sediment, and Biota ......................... 13

Design of the Illinois Environmental Protection Agency and National Water-Quality Assessment

Programs for Major and Trace Elements in Water, Sediment, and Biota ..................................... 13

Illinois Environmental Protection Agency.......................................................... 17

National Water-Quality Assessment Program ....................................................... 17

Methods ......................................................................................... 18

Field and Laboratory Methods................................................................... 18

Water ................................................................................ 18

Suspended and Streambed Sediment........................................................ 19

Biota................................................................................. 19

Statistical Methods............................................................................ 20

Major and Trace Elements in Water, Sediment, and Biota .................................................. 24

Water ...................................................................................... 24

Results of Water-Data Collection, 1978-86,

by Charles G. Crawford and Daniel J. Sullivan.............................................. 24

Results of Water-Data Collection, 1987-90...................................................25

Correlations Among Major and Trace Elements in Water, 1987-90................................31

Seasonal Variations and Long-Term Changes, 1978-90 ......................................... 33

Sediment ................................................................................... 38

Results of Streambed-Sediment Data Collection, 1978-87, 

by John A. Colman....................................................................38

Results of Suspended- and Streambed-Sediment Data Collection, 1987-90..........................40

Correlations Among Major and Trace Elements in Sediment, 1987-90.............................45

Seasonal Variations and Long-Term Changes, 1978-90 .........................................50

Biota....................................................................................... 50

Results of Biotic Data Collection, 1989 and 1990..............................................50

Correlations Among Major and Trace Elements in Biota, 1989 and 1990 ...........................73

Correlations of Element Concentrations Among Water, Sediment, and Biota .............................. 74

Summary and Conclusions........................................................................... 82

Considerations for Future National Water-Quality Assessment Studies........................................ 85

References Cited................................................................................... 86

Appendixes:

A. Results of Chemical Analyses of Water, Sediment, and Biota...................................... 158

B. Minimum Reporting Levels and Analytical Methods for Major and Trace Elements in

Water, Sediment, and Biota............................................................... 250

Contents
FIGURES

1-9. Maps showing:

1. Location of the upper Illinois River Basin ...................................................3

2. Land use in the upper Illinois River Basin ...................................................7

3. Locations of wastewater-treatment plants in the upper Illinois River Basin..........................8

4. Locations of industrial point-source discharges to stream water in the upper Illinois

River Basin ...........................................................................9

5. Locations of sites sampled for major and trace elements in water and biota in the upper

Illinois River Basin, 1978-90 ............................................................ 14

6. Locations of sites sampled for major and trace elements in streambed sediments in the upper

Illinois River Basin, 1978-90 ............................................................ 15

7. Median concentrations of total recoverable copper in the upper Illinois River Basin, 1978-86 .........25

8. Median concentrations of total recoverable aluminum in the upper Illinois River Basin,

1978-86.............................................................................27

9. Mean annual yields of total recoverable boron in the upper Illinois River Basin, 1978-86.............28

10-27. Graphs showing:

10. Total recoverable aluminum and iron concentrations in the upper Illinois River Basin,

1987-90.............................................................................32

11. Seasonal variations in median monthly concentrations of aluminum, arsenic, iron, manganese,

and volatile and total suspended solids in the upper Illinois River Basin, 1987-90...................35

12. Seasonal variations in median monthly concentrations of boron and strontium, and seasonal

variation in median monthly discharge in the upper Illinois River Basin, 1987-90...................36

13. Concentrations of barium and boron at two urban stream sites in the upper Illinois River

Basin, 1978-90 .......................................................................37

14. Probability distributions of chromium, lead, aluminum, and manganese in fine-grained

streambed sediments in the upper Illinois River Basin.........................................43

15. Correlations among selected priority pollutants in suspended sediments from the upper

Illinois River Basin ....................................................................47

16. Correlations between surface area and copper and nickel concentrations in suspended

sediments from the upper Illinois River Basin ...............................................48

17. Correlations between surface area and copper and nickel concentrations in suspended

sediments at two sites in the upper Illinois River Basin ........................................49

18. Effects of sediment surface areas on concentrations of aluminum and calcium in suspended

sediments from the upper Illinois River Basin ...............................................51

19. Relations of aluminum and iron in suspended sediments at two sites in the upper

Illinois River Basin, 1987-90 ............................................................52

20. Element concentrations in common carp and white sucker livers from the upper Illinois

River Basin, 1989-90 ..................................................................53

21. Element concentrations in mollusks from the upper Illinois River Basin, 1989-90...................62

22. Element concentrations in caddisflies and crayfish from the upper Illinois River Basin, 1989..........64

23. Element concentrations in plants from the upper Illinois River Basin, 1989-90 .....................66

24. Relations of concentrations of selected elements in tissue to concentrations in water from

the upper Illinois River Basin, 1989-90 ....................................................76

25. Relations of concentrations of selected elements in tissue to concentrations in suspended

sediment from the upper Illinois River Basin, 1989-90........................................77

26. Relations of concentrations of selected elements in tissue to concentrations in streambed

sediment from the upper Illinois River Basin, 1989-90........................................79

27. Relations of concentrations of selected elements in biota to organic carbon concentrations

in the upper Illinois River Basin, 1989-90 ..................................................80

A1-A3. Box plots showing:

Al. Concentrations of elements dissolved in water in the upper Illinois River Basin, 1987-90........... 159

A2. Total recoverable concentrations of elements in water in the upper Illinois River Basin, 1987-90..... 180

A3. Concentrations of elements in suspended sediments in the upper Illinois River Basin, 1987-90....... 199

VI Contents
TABLES

1. Representative concentrations of selected elements from various background sources........................96

2. Concentrations of selected elements in materials related to domestic sewage treatment in the upper

Illinois River Basin ............................................................................97

3. Total releases of selected elements from wastewater-treatment plants in the Chicago metropolitan area

and in Illinois, and percentage of release from Illinois to the atmosphere and to streams ...................... 97

4. Freshwater acute and chronic water-quality criteria, fish-consumption advisory levels, and Maximum

Contaminant Levels for primary drinking water regulations for 15 elements ...............................98

5. Guidelines for pollutional classification of sediments .................................................98

6. Sites sampled in the upper Illinois River Basin for elements in water, sediment, and biota, 1978-90.............99

7. Element concentrations that exceeded U.S. Environmental Protection Agency freshwater chronic and

acute criteria for total recoverable concentration, 1978-86 ............................................ 103

8. Comparison of total recoverable yields of selected elements in water and in atmospheric deposition in

the upper Illinois River Basin ................................................................... 104

9. Summary of correlation coefficients observed among physical properties and elements in water in the

upper Illinois River Basin, 1987-90 .............................................................. 105

10. Summary of selected trends in element concentrations in stream water in the upper Illinois River

Basin, 1978-90 .............................................................................. 135

11. Statistical summary of concentrations for selected elements in streambed sediments from the

upper Illinois River Basin, 1978-87 .............................................................. 135

12. Tukey studentized range test for ranked concentrations of sieved streambed samples, 1978-87................ 136

13. Tukey studentized range test for ranked concentrations of unsieved streambed samples, 1978-87.............. 136

14. Relation of trace element concentrations in streambed sediments from the upper Illinois River

Basin to background concentrations in streambed sediment and average concentrations in soils ............... 137

15. Correlation coefficients between log-transformed element concentrations in sieved

streambed-sediment samples from the upper Illinois River Basin, 1978-87 ............................... 137

16. Correlation coefficients between log-transformed element concentrations in unsieved

streambed-sediment samples from the upper Illinois River Basin, 1978-87 ............................... 137

17. Factor analysis of log-transformed trace element data from streambed sediments of the upper

Illinois River Basin, 1978-87 ................................................................... 138

18. Summary of element concentrations in water, suspended sediment, streambed sediment, and

biota in the upper Illinois River Basin, 1987-90..................................................... 138

19. Element concentrations in streambed sediments from the upper Illinois River Basin as related to

pollutional classification of Illinois stream sediments ................................................ 139

20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight

National Water-Quality Assessment fixed sites in the upper Illinois River Basin, 1987-90................... 140

21. Correlation coefficients for selected elements in streambed sediments at high-order streams in the

upper Illinois River Basin, 1987 ................................................................. 148

22. Correlation coefficients for selected elements in biota from the upper Illinois River Basin, 1989-90 ........... 149

23. Correlation coefficients observed in physical properties and elements in water and suspended sediment

from the eight National Water-Quality Assessment fixed sites in the upper Illinois River Basin, 1987-90 ....... 151

24. Correlation coefficients for median measurements of physical properties and concentrations of

elements in water and streambed sediment in the upper Illinois River Basin............................... 153

25. Correlation coefficients for 90th-percentile measurements of physical properties and element

concentrations in water and streambed sediment in the upper Illinois River Basin .......................... 154

26. Correlation coefficients for concurrent measurements of physical properties and elements in water

and streambed sediment in the upper Illinois River Basin ............................................. 156

Al. Element concentrations in biota from the upper Illinois River Basin, 1989-90.............................215

A2. Major element concentrations in streambed sediments in the upper Illinois River Basin,

August 1990.................................................................................221

A3. Trace element concentrations in streambed sediments in the upper Illinois River Basin,

August 1990.................................................................................222

Contents VII
A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper

Illinois River Basin, 1987-90 ...................................................................223

A5. Trend-test results and median concentrations for elements in stream water in the upper

Illinois River Basin, 1978-90 ...................................................................231

B1. Minimum reporting levels and chemical analytical methods for major and trace elements in the

upper Illinois River Basin ...................................................................... 251

CONVERSION FACTORS AND ABBREVIATED WATER-QUALITY UNITS

Multiply By To obtain

inch (in.)

mile (mi)

square mile (mi2)

cubic foot per second (ft3/s)

ton per square mile (ton/mi2)

25.4 millimeter

1.609 kilometer

2.590 square kilometer

0.02832 cubic meter per second

2.350 megagram per square kilometer

Temperature in degrees Fahrenheit (°C) as follows:

F=1.8x°C

Abbreviated water-quality units used in this report: Chemical concentrations and water temperature are 

given in metric units. Chemical concentration is given in milligrams per liter (mg/L), micrograms per liter 

(M-g/L) micrograms per gram (|ig/g), or milligrams per kilograms (mg/kg). Milligrams per liter is a unit 

expressing the concentration of chemical constituents in solution as mass (milligrams) of solute per unit volume 

(liter) of water. One thousand micrograms per liter is equivalent to one milligram per liter. For concentrations 

less than 7,000 mg/L, the numerical value is the same as for concentrations in parts per million. Micrograms per 

gram and milligrams per kilograms are in units expressing the concentration of chemical constituents in solution 

as mass (micrograms/milligrams) of constituent per unit mass (gram/kilogram) of a dry sample.

Some masses in this report are given in grams (g). 

given in millimeters (mm).

Pore sizes of membrane filters and screen sizes of sieves are

VIII Contents
Surface-Water-Quality Assessment of the Upper Illinois River 

Basin in Illinois, Indiana, and Wisconsin: Major and Trace 

Elements in Water, Sediment, and Biota, 1978-90

By Faith A. Fitzpatrick, Barbara C. Scudder, J. Kent Crawford, Arthur R. Schmidt, and 

Jennifer B. Sieverling; with contributions from John A. Colman, Charles G. Crawford, and 

Daniel J. Sullivan

Abstract

The distribution of 22 major and trace 

elements was examined in water, sediment, and 

biota in the upper Illinois River Basin in Illinois, 

Indiana, and Wisconsin as part of a pilot National 

Water-Quality Assessment project done by the 

U.S. Geological Survey from 1987 through 1990. 

The 22 elements are aluminum, antimony, arsenic, 

barium, beryllium, boron, cadmium, chromium, 

cobalt, copper, iron, lead, manganese, mercury, 

molybdenum, nickel, phosphorus, selenium, 

silver, strontium, vanadium, and zinc.

Concentrations of U.S. Environmental 

Protection Agency (USEPA) priority pollutants 

among the 22 elements were elevated in the 

Chicago area in all three aquatic components 

(water, sediment, and biota). Further, some of 

the priority pollutants also were found at elevated 

concentrations in biota in agricultural areas in the 

basin. Cadmium, chromium, copper, iron, lead, 

mercury, silver, and zinc concentrations in water 

exceeded USEPA acute or chronic water-quality 

criteria at several sites in the Chicago area. 

Correlations among concentrations of elements 

in water, sediment, and biota were found, but the 

correlation analysis was hindered by the large proportion of observations less than the minimum 

reporting level in water. Those sites where 

water-quality criteria were sometimes exceeded 

were not always the same sites where concentrations in biota were the largest. This relation

indicates that accumulation of these pollutants in 

biota is confounded by complex geochemical and 

biological processes that differ throughout the 

upper Illinois River Basin.

INTRODUCTION

The upper Illinois River Basin was one of four 

surface-water basins selected by the U.S. Geological 

Survey (USGS) in 1986 for the pilot phase of the 

National Water-Quality Assessment (NAWQA) 

program. The NAWQA program was designed to 

(1) provide a nationally consistent description of 

current water-quality conditions for a large part of the 

Nation's water resources, (2) define long-term trends 

in water quality, and (3) identify, describe, and explain 

the major factors that affect observed water-quality 

conditions and trends (Cohen and others, 1988; Hirsch 

and others, 1988). Major and trace elements in water, 

sediment, and biota were identified as principal 

constituents to target because of their possible effects 

on aquatic and terrestrial life, and their relation to the 

transport and accumulation of priority pollutants. 

Assessment of element concentrations in water, 

sediment, and biota will be used to address seven 

NAWQA issues: (1) occurrence of trace elements 

in each component of the aquatic system, (2) spatial 

distribution of elements in each component, 

(3) temporal distributions, (4) background concentrations, (5) relations to different land uses, (6) bioavailability, and (7) development of a national data base.

Introduction
The upper Illinois River Basin drains

r\

10,949 mi of northeastern Illinois, northwestern 

Indiana, and southeastern Wisconsin (fig. 1). 

The upper Illinois River Basin includes three principal streams: the Des Plaines, Kankakee, and 

Fox Rivers. The Des Plaines River flows south 

from Wisconsin and through the city and metropolitan area of Chicago, where it receives water from 

Lake Michigan by way of the North Shore Channel, 

the Chicago Sanitary and Ship Canal, and the 

Calumet Sag Channel. The Kankakee River 

originates in northern Indiana and flows west into 

Illinois to combine with the Des Plaines River. The 

confluence of the two rivers marks the head of the 

Illinois River. The Fox River flows south from 

Wisconsin along the western edge of the basin and 

joins the Illinois River near Ottawa, 111.

The upper Illinois River Basin receives 

numerous anthropogenic inputs of major and 

trace elements from municipal and industrial point 

sources, urban and agricultural runoff, and atmospheric deposition. The urban and industrial areas 

in and around Chicago substantially affected the 

aquatic ecosystem of the upper Illinois River as 

early as 1900, when the flow of industrial and 

domestic wastes was redirected from Lake 

Michigan, Chicago's water supply, to the upper 

Illinois River system (Forbes and Richardson, 

1913,1919; Richardson, 1928). By 1912, fish 

and mussels were virtually absent from streams in 

and downstream from the Chicago area (Forbes and 

Richardson, 1913).

The deterioration in the quality of water in 

the upper Illinois River after 1900 has been due to 

the complex interaction of several factors: depletion of dissolved oxygen by large concentrations of 

organic matter in wastewater from Chicago (Forbes 

and Richardson, 1913; Mathis and Cummings, 1970), 

increased turbidity combined with loss of aquatic 

vegetation in backwater areas (Sparks, 1984), conversion of land in the basin from forest and prairie 

to agriculture (Forbes and Richardson, 1919), and 

construction of navigation dams for maintenance 

of water levels (Sparks, 1984). The additional 

effects of trace elements on the decline in quality 

of the upper Illinois River are unknown; however, 

changes in trace-element concentrations are suspected 

to have had some effect on the biological diversity of 

the upper Illinois River (Mathis and Cummings, 1970).

A variety of institutions have collected large 

amounts of data on the concentration of trace elements 

in water, sediment, and biota in streams in the upper 

Illinois River Basin since the early surveys of changes 

in the biota of the upper Illinois River after the opening 

of the Chicago Sanitary and Ship Canal (Forbes and 

Richardson, 1913,1919; Richardson, 1928; Steffeck 

and Striegl, 1989). These institutions include Federal 

and State research and regulatory agencies, universities, regional planning commissions, and municipal 

wastewater-reclamation facilities. Results from some 

of these surveys were used in the design and planning 

of the upper Illinois River Basin NAWQA program.

Purpose and Scope

This report describes the distribution of 

major and trace elements in water, suspended and 

streambed sediment, and biota in streams of the 

upper Illinois River Basin from April 1978 through 

August 1990. The major objectives of this report 

are twofold. First, the report describes concentrations of major and trace elements in three components (water, sediment, and biota) of the aquatic 

environment in streams of the upper Illinois River 

Basin. Second, the report describes the relations 

between trace-element concentrations in water, 

sediment, and biota so that the effects and fates of 

trace elements throughout the food chain can be 

more completely understood.

Sources of chemical data used in this report 

included samples collected and analyzed during the 

NAWQA pilot study of the upper Illinois River Basin 

from synoptic sites and fixed-sampling sites from 1987 

through 1990 and from the Illinois Environmental 

Protection Agency (IEPA) Ambient Water-Quality 

Monitoring Network from 1978 through 1990.

Included in the report are summary statistics; 

calculated loads and yields; descriptions of seasonal 

variations and trends; correlations among concentrations of trace elements; correlations among concentrations in water, sediment, and biota; and correlations 

among subbasins in the upper Illinois River Basin. 

In addition, element concentrations are compared to 

background concentrations and water-quality criteria. 

The 22 elements examined in this report are aluminum, 

antimony, arsenic, barium, beryllium, boron, cadmium, chromium, cobalt, copper, iron, lead, manganese, 

mercury, molybdenum, nickel, phosphorus, selenium,

2 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
89° 88° 87C 86°

43°

42°

41 C

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M§ ^MCHENR^ ,^'IAKE 

t>E KALB/ -KANE,« [ _ ®\

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EXPLANATION

^ Upper Illinois River 

Basin boundary

-North Shore Channel // ' 

su ~" 1 x -J \^~~~~~- A/ Sr Chicago River : \ : -,

 OGLE? / £ \ *j\ \J\ cr^cago^ Chicago Sanitary and /...., '- ', / 

! ~ f " r ) ^ J^N ^--1 "^a-/ Ship Canal ' 

/ "* - ;_y^sxX ^

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rt r V'^.-' ,--- / ' ,' s ; % XT- M ! / \ ,' %?--y. 1 ..-',' '" / / . i : «,fcc ;*; //

Base from U.S. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic Projection

Standard parallels 33° and 45°, central meridian -89°

20 40 MILES

i r

20 40 KILOMETERS

Figure 1 . Location of the upper Illinois River Basin.

Introduction 3
silver, strontium, vanadium, and zinc. Other chemical constituents and physical properties are referred to 

throughout the discussion where they relate to element 

concentrations.

Acknowledgments

The authors [gratefully] acknowledge the 

analytical assistance of the following persons and 

organizations:

Virginia Carter, U.S. Geological Survey (Reston, 

Va.) Identification of aquatic plant species 

Kevin S. Cummings, Illinois Natural History Survey 

(Champaign, 111.) Identification of mollusks 

Dr. James Gammon, DePauw University 

(Greencastle, Ind.) Collection and identification 

offish species in 1989

U.S. Fish and Wildlife Service (Bloomington, Ind.) 

 Collection and identification of fish species in 

1989

U.S. Fish and Wildlife Service (La Crosse, Wis.)- 

Collection and identification offish species in 1990

Sources of Major and Trace Elements

Element concentrations in water, sediment, 

and biota in streams in the upper Illinois River Basin 

reflect a combination of the geochemistry of the 

surficial deposits in the basin, stream morphology, 

and land-use practices. Principal background sources 

of trace elements in streams in the upper Illinois River 

Basin are rocks, soils, and plant litter. Anthropogenic 

sources include dry and wet deposition of atmospheric 

emissions, industrial and municipal discharges, and 

runoff from agricultural and urban areas. In many 

parts of the upper Illinois River Basin, inputs from 

anthropogenic sources are many times greater than 

inputs from background sources.

Background Sources

In the upper Illinois River Basin, background 

concentrations are not synonymous with natural or 

pristine conditions because virtually all of the upper 

Illinois River Basin is affected by human activities. 

In previous studies of the upper Illinois River Basin, 

background sites for collections of streambed sediment 

were defined as sites upstream from any known pointsource discharge and with a population density less 

than 1,000 people per square mile within a 3-mi radius

of the collection site (John A. Colman, U.S. Geological Survey, written commun., 1989). Kelly and 

Hite (1984, p. 10) defined background as those sites 

"judged unimpacted by point or nonpoint discharge 

with the exception of agricultural nonpoint inputs." 

In this report, the term "background concentrations" 

refers to concentrations that are minimally affected by 

anthropogenic sources.

Elements are released from rocks and soils 

through chemical and biological weathering (Leckie 

and James, 1974; Mattigod and Page, 1983, p. 358). 

Analysis of bulk chemistry of geologic materials can 

indicate potential sources of trace elements (table 1; 

all tables in back of report). Mineralogy and weathering intensity control the release of these elements 

into stream water (Leckie and James, 1974; Drever, 

1988). In addition to directly affecting the traceelement chemistry of a stream, geologic material also 

affects other geochemical properties, such as pH and 

hardness, that indirectly affect trace-element chemistry 

(Drever, 1988).

Release of carbonate from weathering of 

limestone and dolomite typically increases pH, 

hardness, and alkalinity. Streams in the upper 

Illinois River Basin have eroded through soils and 

unconsolidated deposits into carbonate-rich bedrock 

in many areas. These rocks are mainly composed 

of dolomite interbedded with lesser amounts of limestone, sandstone, shale, and coal (Willman and others, 

1975; Mades, 1987). Downcutting by the Illinois 

River and the lower Fox River has exposed limestone 

and dolomite of Ordovician and Silurian age and 

shale, limestone, and coal of Pennsylvanian age 

(Willman, 1973; Willman and others, 1975; Mades, 

1987). Dolomite of Silurian age is exposed in 

deep quarries near Chicago; along the valleys of the 

lower Des Plaines, lower Kankakee, lower Du Page, 

and lower Fox Rivers; and in the excavated channel of 

the Chicago Sanitary and Ship Canal (Willman, 1973; 

Willman and others, 1975; Gross and Berg, 1981; 

Mades, 1987). Limestone, shale, and sandstone of 

Mississippian and Devonian age crop out along the 

Iroquois River and some of its tributaries (Willman 

and others, 1975; Mades, 1987).

Typical concentrations of elements in 

carbonate rocks, sandstone, and shales are listed 

in table 1. These concentrations reflect averages 

for the United States. No data are available for 

rocks in the upper Illinois River Basin alone; 

however, consistent information is available for

4 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
background stream concentrations in Illinois, as well 

as data collected nationwide for soil concentrations. 

Statewide background distributions that reflect 

Illinois geology have been identified by Kelly and 

Kite (1984). Aluminum and iron are abundant in 

rocks; copper, vanadium, and zinc are less abundant 

but still common in rocks (Moore and Ramamoorthy, 

1984; City of Chicago and Illinois Environmental 

Protection Agency, 1985) (table 1). Strontium 

concentrations are typically larger in carbonate rocks 

than in other rock types (table 1) (City of Chicago and 

Illinois Environmental Protection Agency, 1985). 

Weathering of coal-bearing sedimentary rocks can 

release arsenic (Kelly and Kite, 1984). Beryllium is 

rare in crustal rocks (City of Chicago and Illinois 

Environmental Protection Agency, 1985; Hem, 1985).

Unconsolidated deposits blanket the bedrock 

surface and are variable in thickness and lithology. 

The surficial deposits are mainly glacial, glaciofluvial, 

or glaciolacustrine sediments that were deposited 

during the last glaciation (Willman and Frye, 1970; 

Lineback, 1979; Hansel and others, 1986). The 

mineralogy of the deposits and soils reflects the underlying bedrock in the vicinity (table 1); thus, these 

deposits also are carbonate rich. The most abundant 

type of glacial deposit in the upper Illinois River Basin 

is fine-grained till (Willman and Frye, 1970; Lineback, 

1979). Major rivers in the basin generally flow 

through narrow bands of coarse-grained outwash and 

lacustrine deposits surrounded by silty and clayey 

glacial till. An exception is the Kankakee River, 

which flows through an areally extensive, coarsegrained outwash plain in Indiana (Hansel and others, 

1986). The outwash plain consists of extensive sands 

covered in places by either eolian sand or organic-rich 

muck and peat. Because of this, the Kankakee River 

and its tributaries carry a greater sand load than other 

major rivers in the basin (Gross and Berg, 1981). 

The Iroquois River subbasin contains mainly glaciolacustrine deposits (Lineback, 1979; U.S. Department of 

Agriculture, Soil Conservation Service and Purdue 

University Agricultural Experiment Station, 1982).

Ground water from shallow bedrock aquifers 

contributes to the base flow of the major streams in the 

basin, although the volume of ground-water contribution has not been quantified. Extensive aquifers in 

the Ordovician and Silurian bedrock are known to 

contribute to the base flow of the Fox River in Kane 

County (Fitzpatrick and others, 1992). Ground water 

from bedrock is probably contributing to other stream

reaches as well, in contact with bedrock. The 

geochemistry of rocks in the aquifer is reflected 

in the geochemistry of the ground water. In the 

upper Illinois River Basin, accessory feldspar in 

sandstone may be the source of barium in ground 

water (Gilkeson and others, 1983). Sand and 

gravel aquifers are not as extensive as the bedrock 

aquifers; nevertheless, they also contribute to the 

base flow of streams where they are not hydraulically 

separated from the streambed by fine-grained glacial 

till, lacustrine deposits, or fine-grained alluvium.

Vegetation can change the geochemistry of 

soils by concentrating some elements and depleting 

others. Leaves and forest material, for example, 

can contain significant amounts of manganese, 

which may affect the manganese concentrations in 

streams (Hem, 1964, p. B2-B3; Bobo and Renn, 

1980) (table 1). Plant litter and animal feces release 

phosphorus (Striegl and Cowan, 1987). Humic 

acids from plants can affect the pH of soils, which 

alters the solubility and release mechanism of some 

elements.

Clay minerals in fine-grained sediment, which 

are transported by the streams and deposited in pools, 

serve as media for adsorption of trace elements. 

Organic material also accumulates in these pools and 

may concentrate trace elements. Flood plain deposits 

and backwater sediments also may be resuspended 

during high flow and renew the source of fine-grained 

material available for trace-element adsorption. 

Background concentrations of selected elements in 

water and streambed sediments in the middle Illinois 

River and three nonindustrial tributaries are shown in 

table 1. Background concentrations of elements were 

larger in streambed sediment than in water; however, 

they were similar to concentrations of the elements 

in soils and surficial material (table 1). For example, 

concentration of arsenic in streambed sediments 

(2-14 mg/kg) did not differ substantially from 

background concentrations reported for precultural 

sediments from North American lakes (0.6-11 mg/kg) 

(Forstner and Wittman, 1979).

Anthropogenic Sources

Elements from anthropogenic sources are 

transported directly to the stream environment 

through point-source discharge and indirectly 

through dry and wet atmospheric deposition and 

surface runoff. Significant human contributions 

of elements to streams in the upper Illinois River

Introduction
Basin began in the 1870's and were caused by the 

growth and expansion of agriculture in the basin and 

by growth and expansion of industrial and urban areas 

in and near Chicago, 111., and Gary, Ind. Navigational 

dams were constructed on the Des Plaines, Kankakee, 

Fox, and Illinois Rivers, which caused large volumes 

of fine-grained sediment to accumulate (U.S. Army 

Corps of Engineers, Chicago District, 1987).

Urban areas contribute trace elements to streams 

in the upper Illinois River Basin through atmospheric 

deposition, point-source discharges, and nonpointsource runoff (Mathis, 1976). Urban land in the 

basin (fig. 2) is estimated to be about 8 percent industrial, 59 percent residential, 19 percent commercial, 

and 15 percent undetermined urban land. The area 

drained by the Calumet River system contains some 

of the most heavily industrialized land in the Nation; 

petroleum refining and steel manufacturing are the 

dominant industries (City of Chicago and Illinois 

Environmental Protection Agency, 1989). Previous 

studies of streams near urban areas have concluded 

that, in general, elevated concentrations of copper, 

iron, mercury, and zinc are associated with urban 

activities (Leed and Belanger, 1981; Kelly and Kite, 

1984). Cadmium, chromium, copper, iron, lead, 

nickel, and zinc concentrations were all significantly 

larger in bottom sediments of the Illinois River than in 

bottom sediments of the nonindustrial-area streams, 

and chromium, cobalt, copper, and lead concentrations 

were elevated in Illinois River water (Mathis and 

Cummings, 1970).

Base flows of most streams in the Chicago area 

consist partly of industrial or municipal effluent or 

both. Streams and their tributaries where stream 

quality is particularly affected by effluent from point 

discharges include the Des Plaines River, the tributaries that flow along the shore of Lake Michigan 

through inner Chicago, the Chicago Sanitary and Ship 

Canal, the Calumet River system, and the Du Page 

River. Examples of point-source discharges include 

effluent from wastewater-treatment plants (fig. 3), 

manufacturing plants and other industries (fig. 4), 

chemical spills, and sewer outfalls. Few streams in 

the upper Illinois River Basin do not receive some kind 

of point discharge. Wastewater-treatment plants 

remove some of the elements from sewage, but some 

element concentrations are commonly elevated in 

wastewater from the treatment plants relative to 

background concentrations (table 2) (Williams and 

others, 1974). Copper, chromium, nickel, and zinc

are common trace elements supplied by domestic 

sewage (Williams and others, 1974). Effluent from 

iron and steel manufacturing plants can contain 

copper, chromium, lead, and nickel (Forstner and 

Wittman, 1979; Salomons and Forstner, 1984). 

Effluent from other metal industries, including 

nonferrous primary producers, electroplating industries, and ferrochrome industries, commonly includes 

copper, chromium, lead, nickel, silver, and zinc (Kelly 

and Kite, 1981,1984; Moore and Ramamoorthy, 

1984). Ground-wood pulping processes release 

barium, chromium, and zinc (Rickert and others, 1977; 

Kelly and Kite, 1981; City of Chicago and Illinois 

Environmental Protection Agency, 1985). Lead and 

cadmium are released from battery-manufacturing 

plants (Kelly and Kite, 1981,1984; Moore and 

Ramamoorthy, 1984).

Several possible disposal methods of the 

elements and related compounds complicate the 

direct relation of the amounts of elements released 

by industries and the amounts that arrive in streams 

in the Chicago area. Industrial wastes are disposed 

of through air emissions, water discharges, wastewater-treatment plants, landfills, and offsite transfers 

(table 3). In the Chicago metropolitan area, 

most of the elements are disposed of primarily 

through offsite transfers and secondly through land 

disposals. Offsite transfer means that the waste 

was disposed of somewhere outside of the Chicago 

area. Only a small percentage of the total amount 

released is discharged directly to streams, air, or a 

wastewater-treatment plant.

Sources that contribute elements to the 

atmosphere in the Chicago metropolitan area 

include devices that burn fossil fuels, metallurgical 

coke manufacturing ovens, iron and steel manufacturing facilities, waste incinerators, and cement 

manufacturing plants (Winchester and Nifong, 1971). 

Fossil-fuel combustion releases a variety of trace 

elements, including aluminum, arsenic, barium, 

cadmium, chromium, cobalt, iron, lead, mercury, 

molybdenum, nickel, selenium, vanadium, and 

zinc (Winchester and Nifong, 1971; Kagey and 

Wixson, 1983, p. 473^75; Kelly and Kite, 1984; 

Moore and Ramamoorthy, 1984; City of Chicago 

and Illinois Environmental Protection Agency, 1985). 

Metallurgical coke manufacturing ovens and 

other metal producers emit aluminum, cadmium, 

chromium, copper, iron, lead, and zinc into the 

atmosphere (Winchester and Nifong, 1971;

6 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
EXPLANATION

URBAN LAND

AGRICULTURAL LAND 

| FOREST 

 BASIN BOUNDARY

LAKE MICHIGAN

Chicago Sanitary and ?*»« canal

MICHIGAN 

INDIANA

Calumet Sag 

Channel

Base from U.S. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic projection

Standard parallels 33° and 45°, central meridian -89°

Figure 2. Land use in the upper Illinois River Basin.

40 MILES

20 40 KILOMETERS

Introduction 7
EXPLANATION

BASIN BOUNDARY

WASTEWATER-TREATMENT 

PLANT POINT-SOURCE 

DISCHARGE SITE

i>/^y °°o le

V W<D ,-, /

LAKE MICHIGAN

Chicago Sanitary and 

Ship Canal

/ ^ . ~-N ;

'/0 -r^'-V

Base from US. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic projection

Standard parallels 33° and 45°, central meridian -89°

40 MILES

20 40 KILOMETERS

Figure 3. Locations of wastewater-treatment plants in the upper Illinois River Basin. (Locations compiled 

from the Illinois State Water Use data base, John LaTour, U.S. Geological Survey, written commun., 1988; and 

from the Industrial Facilities Discharge data base, Phillip Taylor, U.S. Environmental Protection Agency, oral 

commun., 1988.)

8 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
EXPLANATION

BASIN BOUNDARY

INDUSTRIAL POINT-SOURCE 

DISCHARGE SITE

Chicago Sanitary and 

Ship Canal

v7.nw

 '... ', ' ° j S. ,_-U 1 - - . '"o / A-«_ ' - --"x . :

, I V yw VJ I >

- vI^./V/ ^<.

-..,. \ '-.-% ~LJ 03

Base from US. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic projection

Standard parallels 33° and 45°, central meridian -89°

40 MILES

40 KILOMETERS

Figure 4. Locations of industrial point-source discharges to stream water in the upper Illinois River 

Basin. (Locations compiled from the Illinois State Water Use data base, John LaTour, U.S. Geological 

Survey, written commun., 1988; and from the Industrial Facilities Discharge data base, Phillip Taylor, 

U.S. Environmental Protection Agency, oral commun., 1988.)

Introduction
Moore and Ramamoorthy, 1984). Iron and steel 

manufacturing releases atmospheric emissions of 

aluminum, arsenic, cadmium, copper, iron, lead, 

manganese, nickel, and zinc (Winchester and Nifong, 

1971; Kelly and Kite, 1981, 1984; Moore and 

Ramamoorthy, 1984). Waste incineration releases 

mercury, nickel, and zinc (Moore and Ramamoorthy, 

1984). Cement manufacturing plants and refractory 

brick producers release aluminum, chromium, and iron 

(Winchester and Nifong, 1971; Moore and 

Ramamoorthy, 1984).

Runoff from urban areas commonly contains 

residues from gasoline, motor oil, tires, brake linings, 

galvanized metal, nails, painted surfaces, pesticides, 

and fertilizers (Moore and Ramamoorthy, 1984; 

Striegl and Cowan, 1987). Arsenic, chromium, 

copper, iron, mercury, and phosphate are associated 

with runoff from urban areas (Leed and Belanger, 

1981; Kelly and Kite, 1981, 1984; Moore and 

Ramamoorthy, 1984). Traffic-related sources 

contribute copper, lead, and zinc to urban runoff 

(Striegl and Cowan, 1987). Building materials 

commonly release zinc (Kelly and Kite, 1984).

Runoff from urban and agricultural areas alike 

can be affected by fertilizers and pesticides, which 

may release arsenic, copper, mercury, phosphorus, 

and zinc (Richardson and others, 1978; Kelly and 

Kite, 1981,1984; Moore and Ramamoorthy, 1984). 

Agricultural land, which accounts for approximately 

75 percent of the basin, mainly consists of cropland; 

the principal crops produced are corn and soybeans 

(Anderson and others, 1976; Feagas and others, 1983) 

(fig. 4). Methylmercury acetate and methoxyethyl 

mercury acetate were previously used on corn, but 

these pesticides are now banned. Sodium arsenate 

was used as an insecticide, but its use has been discontinued (Berg, 1976; Kelly and Kite, 1981; Sine, 1992). 

Sodium arsenite is used as a fungicide, herbicide, and 

insecticide, but its use decreased before the 1970's 

because of its extreme toxicity and solubility (Berg, 

1976).

Runoff from coal-mined areas can have elevated 

concentrations of arsenic, boron, iron, manganese, and 

zinc (Kelly and Kite, 1981, 1984; Brabets, 1984; 

Moore and Ramamoorthy, 1984). Coal has been 

mined by surface and subsurface methods in the southwestern part of the upper Illinois River Basin. The 

coal-mining district extends from the confluence of the 

Kankakee and Des Plaines Rivers southwest along the 

valley of the Illinois River to the basin boundary, and

south of the Illinois River in the Mazon River Basin 

(Smith, 1968). Previous studies have shown that 

large concentrations of aluminum, iron, manganese, 

and zinc were found in samples from streams downstream from coal-mining areas in other parts of 

Illinois, particularly in acidic environments (Brabets, 

1984). In-place neutralization, however, greatly 

reduces metal concentrations in mine runoff (Brabets, 

1984), especially in the upper Illinois River Basin 

where limestone is abundant.

Geochemistry of Major and Trace Elements

The 22 elements examined in this report 

are present in major and trace amounts in surface 

water. Normally, major elements are defined as 

elements that are present in water at concentrations 

of greater than 1 mg/L (Hem, 1985). Of the 

22 elements, major elements include boron and 

three metals: aluminum, iron, and manganese. 

The remaining 18 elements generally are present at 

concentrations less than 1 mg/L in water and are 

considered minor or trace elements. Most of the 

18 trace elements are metals; exceptions are antimony, 

arsenic, and selenium. Lead and mercury are 

generally referred to as heavy metals in the literature, 

although many authors use the terms heavy metals and 

trace elements interchangeably. Minor, or trace, 

elements also may be present at concentrations greater 

than 1 mg/L as a result of weathering of ore-bearing 

rocks and sediments, discharge of industrial and 

municipal effluents, urban and agricultural runoff, and 

atmospheric deposition.

Concentrations of elements in the water 

and sediment depend not only on the sources of 

the elements but also on the complex interaction of 

chemical and biological processes in the stream that 

receives the elements (Williams and others, 1974). 

These processes affect the speciation and the partitioning of an element in the aquatic environment.

The species of these elements affect their availability and toxicity to humans and aquatic life (Batley, 

1983). Speciation refers to the distribution between 

chemical species and includes the valence or oxidation 

state of an element. Speciation is affected by hydrogen ion activity, oxidizing or reducing conditions, 

temperature, alkalinity, hardness, chlorinity, complexation with other compounds, and biochemical activity.

Elements can be partitioned among the 

dissolved or particulate phases in differing amounts,

10 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
depending on a variety of factors including hydrogen 

ion activity, oxidizing or reducing conditions, 

adsorption to hydrous oxides, concentration of organic 

matter, biological activity, hydraulic energy, and the 

nature of the substrate (Williams and others, 1974; 

Elder, 1988; Horowitz, 1991). In general, antimony, 

arsenic, barium, boron, molybdenum, selenium, and 

strontium are found in the dissolved phase, whereas 

aluminum, chromium, iron, lead, mercury, vanadium, 

and zinc are mainly found in the paniculate phase. 

Cadmium, cobalt, copper, manganese, and nickel are 

commonly found in both phases (Horowitz, 1991).

Elements may transfer from one phase to 

another through changes in precipitation/dissolution, 

sorption/desorption, electrostatic attraction, hydrogen 

ion activity and ionic strength of the solution, concentration of complex-forming ligands, and diagenesis of 

particulates over time (O'Connor and Kester, 1975; 

Forstner and Salomons, 1983). The strength of 

electrostatic attraction depends on particle or ligand 

composition, concentration, and absorptive properties; 

solution properties of hydrogen ion activity and 

oxidation-reduction reactions; and the composition, 

concentration, and reactivity of the ions in solution.

Streambed sediments in the upper Illinois River 

are known to be enriched with heavy metals compared 

to water (Mathis, 1976). For example, Presley and 

others (1980) found that greater than 87 percent of the 

total metal load carried in the lower Mississippi River 

is transported in the sediment load. Some metals that 

are adsorbed onto paniculate matter in the bottom 

material may be desorbed back into the water column, 

depending on the chemical composition of the water; 

bottom sediments also can be resuspended by high 

streamflow and wave action in shallow backwater 

areas.

Dissolved species of trace elements are of 

particular concern because they are more readily incorporated into potable water supplies than paniculate 

species are. Dissolved species have a strong sorption 

affinity toward three types of materials: organic 

detritus, clay-mineral particles, and iron-manganese 

oxide coatings (Elder, 1988). These materials can be 

transported in suspension, or they can settle and 

accumulate on the stream bottom.

Elements can be adsorbed onto organic ligands, 

iron or manganese hydroxides or oxides, and clay 

minerals through ion exchange, or they can precipitate 

as solid mineral phases (Forstner and Salomons, 

1983). Physical adsorption occurs at external

surfaces, inner surfaces, or pores of particulates or 

colloids (Forstner and Salomons, 1983). Adsorption 

generally occurs faster than mineral dissolution and 

precipitation (Stumm and Morgan, 1981; Drever,

1988). Rates of adsorption may be greatly affected 

by small fluctuations in hydrogen ion activity 

(Forstner and Salomons, 1983). If pH is lowered, 

particle-surface charges and attractive forces are 

reduced, and surfaces can no longer hold positively 

charged metals (Michnowsky and others, 1982). 

Diurnal fluctuations in photosynthetic activity, which 

in turn affect pH, can cause substantial changes in 

dissolved element concentrations (Fuller and Davis,

1989). In addition to pH fluctuations, magnesium 

ions in solution interfere with adsorption of other trace 

elements by competing with them for the same 

adsorptive sites (O'Connor and Kester, 1975).

The adsorption capacities of elements are 

dependent on the reactivity and solubility of each 

element and paniculate characteristics such as 

substrate source and thermodynamic instability, 

particle size, surface area, and surface charge. In 

general, lead has the largest binding capacity of all the 

trace elements, followed by copper; cadmium has the 

weakest binding capacity (Alberts and others, 1984). 

The adsorption affinity of lead can be attributed to its 

comparatively small hydrated radius and the adsorption preference of hydrolyzed species over divalent 

metal cations (Holden, 1989). Differences in characteristics of particulate matter and other environmental 

factors cause some differences in ranking the relative 

adsorption capacities of elements for iron and manganese oxides, organic ligands, and clay minerals 

(Collinson and Shimp, 1972; Leed and Belanger, 

1981; Forstner and Salomons, 1983; Alberts and 

others, 1984; Bailey and Rada, 1984; Buhl and 

McConville, 1984; Johnson, 1986; Horowitz and 

Elrick, 1987; Holden, 1989).

Precipitation of element compounds can result 

from changes in conditions of pH, oxidation potential, 

and concentrations of precipitating compounds and 

elements (Forstner and Salomons, 1983). Precipitation also depends on the solubilities of the trace 

elements involved. Precipitation of element 

compounds can occur when waters from different 

sources mix, such as when two rivers with different 

water and sediment chemistry join or when ground 

water under reducing conditions comes in contact with 

oxidized surface water.

Geochemistry of Major and Trace Elements 11
Fate and Effects of Major and Trace Elements 

on Aquatic Biota

The complex interaction of physical, 

chemical, and biological processes that affect the 

speciation, and partitioning of elements can have 

profound effects on the availability of elements to 

biota, or bioavailability, as well as on their bioaccumulation and toxicity (Batley, 1983). The geochemistry 

of elements in sediment and in water greatly affects 

their bioavailability. Most elements in the aquatic 

environment exist for only a short time in the dissolved 

phase, the most important phase for uptake of elements 

by biota. Instead, elements are generally bound to 

particulates or organic and inorganic compounds and 

so are less bioavailable (Rand and Petrocelli, 1985; 

Elder, 1988; Luoma, 1989). Recent research has 

indicated that cadmium, copper, nickel, lead, and zinc 

in sediments may not be available to biota if acid 

volatile sulfide concentrations are sufficient to bind 

these elements (Ankley and others, 1992). Biota, 

however, may alter the species of an element, and 

thereby its bioavailability, through methylation, 

chelation, complexation, absorption, oxidation, and 

reduction (Forstner and Salomons, 1983; Smies, 

1983). Elements that are known to undergo methylation include arsenic, mercury, selenium, and lead 

(Demayo and others, 1982; Smies, 1983; Moore and 

Ramamoorthy, 1984;Eisler, 1987,1988a, 1988b). 

Although direct measurement of the amount of an 

element that is bioavailable is not currently possible, 

measurement of bioaccumulation of most elements is 

relatively straightforward (Luoma and Carter, 1991).

Biological uptake may be from elements that are 

dissolved in water, from suspended sediment to which 

elements are adsorbed, from elements bound to bottom 

material, or from consumption of other organisms. 

Although uptake from the paniculate phase is less 

efficient than from the dissolved phase, the concentration of elements in the particulate phase is larger 

and, therefore, can be very important (Luoma, 1989). 

Uptake from the dissolved or particulate phases can 

occur in a variety of ways. Adsorption, the binding 

of an element to a surface, can be especially large for 

bacteria and diatoms because of their large surface-tovolume ratio. Adsorption may be followed by 

absorption, the movement of an element across cell 

membranes into the organism (Spacie and Hamelink, 

1985). Submerged aquatic plants, such as pondweed, 

can absorb elements from water and from streambed 

sediments (Sculthorpe, 1967). Uptake of elements

into plant roots and subsequent transfer to stems and 

leaves can remobilize bound trace elements buried 

below the streambed surface, elements that were previously unavailable to other biota (Buhl and McConville, 

1984). Invertebrates and fish can take up trace 

elements by absorption from water, ingestion of food 

and suspended particulates that contain trace elements, 

or adsorption of elements onto gill or other body 

surfaces. This uptake may be followed by diffusion 

through gills and linings of the gut and mouth of 

aquatic invertebrates and fish (Luoma, 1983; Rand and 

Petrocelli, 1985; Clements, 1991). Invertebrates can 

also be important in remobilizing trace elements back 

into the water column, where they would then be 

available for uptake by other organisms (Reynoldson, 

1987).

Bioaccumulation of trace elements refers to 

their incorporation into the tissues of biota. Bioaccumulation can result in toxic effects such as 

decreased reproduction, mutations, or ultimately 

death. Important biotic factors affecting bioaccumulation and toxicity include the type and species of 

organism, as well as its age, sex, health, reproductive 

cycle, parasitism, acclimation, and a variety of internal 

biological processes (Phillips, 1980; Sprague, 1985; 

Cain and Luoma, 1990). After uptake, elements 

can be transported to another location in the body 

for storage or to organs that will either metabolize or 

eliminate the element. Elements may accumulate to 

different concentrations in various tissues, such as the 

liver, kidney, gills, and skin or cuticle. The liver is 

the primary site for metabolism of contaminants, and 

the kidney and liver are the main organs responsible 

for elimination of contaminants. Biota are able to 

regulate internal concentrations of some elements at 

small to moderate concentrations through uptake and 

elimination. The rate of elimination of trace elements 

from biota can be very important in reducing bioaccumulation and toxicity (Guthrie, 1980; Matthews, 1980; 

Rand and Petrocelli, 1985).

Toxicity to trace metals can range from 

sublethal effects, such as a decrease in growth, to 

acute effects, including death. Organometals, 

mainly alkyl metals such as methylmercury, are more 

toxic than most other forms of elements because they 

are lipid soluble, are easily mobilized through the food 

chain, and tend to bioaccumulate more. Although 

inorganic mercury in aquatic systems has not been 

shown to be toxic, microorganisms are capable of 

transforming it to methyl mercury compounds that are

12 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
highly biologically mobile and toxic (Eisler, 1987). 

Many trace elements are essential nutrients for most 

organisms at small concentrations but may be toxic 

at excessive concentrations. Elements of this type 

include cobalt, copper, chromium, iron, manganese, 

nickel, molybdenum, selenium, tin, and zinc. 

Cadmium, mercury, and lead are nonnutritive and 

can be toxic at very small environmental concentrations (Donaldson, 1980; Batley, 1983; Leland and 

Kuwabara, 1985; Eisler, 1988b). Arsenic may be 

nutritionally essential or beneficial in small doses 

(Eisler, 1988a).

Trace elements in water and bottom material 

can biomagnify, or increase in concentration, at higher 

levels of organization in the food chain, even though 

they may have entered the aquatic system at subtoxic 

levels. Biomagnification can proceed from primary 

producers (such as diatoms) to benthic and filterfeeding organisms to fish and, eventually, to 

humans. Once bound in aquatic plant tissues, 

accumulated elements can be transferred to other 

organisms through grazing or released to the aquatic 

environment through microbial decomposition of plant 

tissues (Buhl and McConville, 1984). Organisms that 

feed on the grazers may continue to bioaccumulate 

concentrations of the elements. Examples of the 

effects of biomagnification include (1) methylmercury 

poisoning in humans, in Minamata, Japan, from 

consumption of contaminated shellfish (Takeuchi, 

1972; Forstner and Wittman, 1979); (2) itai-itai disease 

in humans living in Toyama Prefecture, Japan, from 

consumption of rice irrigated with cadmium-rich water 

(Friberg and others, 1974); (3) large concentrations of 

mercury in fish in Sweden and America, from industrial effluent and atmospheric deposition (Sana and 

McKinley, 1975); and (4) reproductive problems in 

aquatic birds at Kesterson National Wildlife Refuge in 

California, from accumulation of selenium (Ohlendorf, 

1986; Presser and Ohlendorf, 1987).

Criteria and Guidelines for Element 

Concentrations in Water, Sediment, and Biota

Of the 22 elements examined in this study, 

12 are listed as priority pollutants by the U.S. Environmental Protection Agency (USEPA): antimony, 

arsenic, cadmium, beryllium, chromium, copper, 

lead, mercury, nickel, selenium, silver, and zinc 

(U.S. Environmental Protection Agency, 1986). 

Freshwater acute and chronic water-quality criteria,

fish-consumption advisory levels, and Maximum 

Contaminant Levels established by USEPA for these 

elements in drinking water are listed in table 4. 

Barium, iron, and manganese, although not considered 

priority pollutants, are addressed in some partial 

criteria for drinking water, freshwater chronic levels, 

and fish consumption. Arsenic(V), arsenic(IH), 

chromium(VI), and chromium(IH) are addressed by 

separate freshwater acute and chronic water-quality 

criteria based on valence. In addition, arsenic and 

beryllium are known carcinogens. Criteria for six 

elements in water are dependent on hardness, because 

increases in hardness reduce the toxicity of these 

elements (City of Chicago and Illinois Environmental 

Protection Agency, 1985; U.S. Environmental 

Protection Agency, 1986). Criteria in table 4 are 

based on a hardness of 100 mg/L. Hardness of 

stream water from the upper Illinois River Basin 

ranges from approximately 100 to 480 mg/L. Standards were established by the USEPA for the maximum acceptable concentrations of trace elements in 

unfiltered water.

Although no sediment criteria have been 

accepted by USEPA at this time, two guidelines are 

frequently used to evaluate concentrations of the 

priority pollutants in sediments (table 5). The 

USEPA (1977) established guidelines for the classification of Great Lakes Harbor sediments that are used 

for evaluating the amount of pollution before dredging 

and cleanup. In addition, the Ontario Ministry of 

Environment and Energy established guidelines for the 

protection and management of aquatic sediments in 

Ontario (Persaud and others, 1993).

DESIGN OF THE ILLINOIS 

ENVIRONMENTAL PROTECTION AGENCY 

AND NATIONAL WATER-QUALITY 

ASSESSMENT PROGRAMS FOR MAJOR 

AND TRACE ELEMENTS IN WATER, 

SEDIMENT, AND BIOTA

Data included in this report are from water, 

sediment, and biological samples collected by the 

USGS NAWQA program and the IEPA. Details 

about the design of the IEPA and NAWQA sampling 

programs are given in the following sections. Site 

characteristics are listed in table 6, and site locations 

are shown in figures 5 and 6.

Design of the Illinois Environmental Protection Agency and National Water-Quality Assessment Programs for Major and Trace 13
EXPLANATION

BASIN BOUNDARY

NATIONAL WATER-QUALITY 

ASSESSMENT MONTHLY 

FIXED SITE

TISSUE-COLLECTION SITE

ILLINOIS ENVIRONMENTAL 

PROTECTION AGENCY 

BIMONTHLY AMBIENT 

WATER-QUALITY 

COLLECTION SITE

WISCONSJN-j^ 

ILLINOIS =' ^"

SITE NUMBER (refer to table 6)

LAKE MICHIGAN

Chicago Sanitary and 

Ship Canal

Calumet Sag 

Channel

Base from US Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic projection

Standard parallels 33° and 45°, central meridian -89°

40 MILES

20 40 KILOMETERS

Figure 5. Locations of sites sampled for major and trace elements in water and biota in the upper Illinois River 

Basin, 1978-90.

14 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
EXPLANATION

BASIN BOUNDARY

SIEVED STREAMBED SEDIMENTS 

COLLECTED BY ILLINOIS 

ENVIRONMENTAL PROTECTION 

AGENCY, 1982-87

UNSIEVED STREAMBED SEDIMENTS 

COLLECTED BY ILLINOIS 

ENVIRONMENTAL PROTECTION 

AGENCY, 1978

LAKE MICHIGAN

Chicago Sanitary and 

<o Canal

Calumet Sag 

Channel

-s ^f

from US Geological Survey 

1:100,000 Digital Line Graphs 

Albers Equal-Area Conic projection 

Standard parallels 33° and 45°, central meridian -89°

40 MILES

20 40 KILOMETERS

Figure 6. Locations of sites sampled for major and trace elements in streambed sediments in the upper Illinois 

River Basin, 1978-90.

Design of the Illinois Environmental Protection Agency and National Water-Quality Assessment Programs for Major and Trace 15
89° 88° 86°

43'

42°

41 <

JtD

a/ 

/

r" o^D -.

-^09 a /

- . -^ 

 **- i-r-Y' /Q /U (^f :

,,,-0-^DA ,-1

' -oV ^VaA (._

87° ____________ I 

EXPLANATION

 BASIN BOUNDARY

STREAMBED-SEDIMENT 

SYNOPTIC SURVEY 

SITE SAMPLED BY THE 

U.S. GEOLOGICAL SURVEY

Chicago Sanitary and 

Canal

- --..^ <; .7; i ° Q

Base from U.S. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic projection

Standard parallels 33° and 45°, central meridian -89°

Figure 6. Continued.

40 MILES

20 40 KILOMETERS

16 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Illinois Environmental Protection Agency

Since approximately 1978, the IEPA has 

collected water samples for analysis of dissolved and 

total recoverable concentrations of major and trace 

elements at 38 sites in the upper Illinois River Basin at 

6-week intervals (fig. 5; table 6). These sites are part 

of the Illinois Ambient Water-Quality Monitoring 

Network and are on main-stem streams in Illinois 

(except for one site on the Illinois-Indiana State 

line). From 1987 through 1990,6 of the 38 sites 

were sampled at 4-week intervals by the USGS as 

part of the NAWQA program. Samples were analyzed for 17 of the 22 elements discussed in this report; 

analysis for antimony, selenium, and molybdenum, 

and dissolved arsenic and mercury were not done.

Streambed-sediment data for major and trace 

elements were collected by the IEPA at 103 sites from 

approximately 1978 through 1987 (fig. 6). Although 

many elements in streambed sediments were analyzed 

for by the IEPA, only 10 elements were measured in 

nearly every sample: arsenic, cadmium, chromium, 

copper, iron, lead, manganese, mercury, phosphorus, 

and zinc. Most of the sediment-data sites are clustered along main-stem streams in the northern part of 

the Illinois part of the upper Illinois River Basin, 

including the Fox, Du Page, Des Plaines, North Branch 

Chicago, Calumet, and Illinois Rivers.

National Water-Quality Assessment Program

Samples for dissolved and total recoverable 

concentrations of trace elements in water were 

collected monthly at the eight NAWQA fixed sites 

from 1987 through 1990. Suspended-sediment 

samples were collected bimonthly (table 6; fig. 5). 

Details about the sampling design and the qualityassurance results are given in Sullivan and Blanchard 

(1994). The fixed sites are all at established streamflow-gaging stations and generally are near the mouths 

of major rivers. Two fixed sites are on the Fox River 

(sites 89 and 99), and one site each is on the Kankakee 

River (site 14), the Iroquois River (site 28), the 

Des Plaines River (site 40), the Chicago Sanitary and 

Ship Canal (site 55), the Du Page River (site 69), and 

the Illinois River (site 76). The sites were chosen to 

maximize the information obtained from calculating 

mass balances within the upper Illinois River Basin 

and to document the transport of constituents (Sullivan 

and Blanchard, 1994). Six of the eight fixed sites

(sites 14,28, 69, 76, 89, and 99) were established 

IEPA sampling sites that the USGS sampled for the 

IEPA during 1987 through 1990.

Data from the total recoverable phase in water 

were available for all 22 trace elements. Samples for 

analysis of dissolved antimony and molybdenum were 

collected seasonally (four times a year) instead of 

monthly. Dissolved and total recoverable mercury 

data were few because of problems with sample 

contamination during processing. Only a few observations were available for selenium concentrations. 

Suspended-sediment samples were analyzed for 

17 of the 22 elements examined in this report; 

barium, boron, mercury, selenium, and strontium 

were excluded.

Streambed-sediment samples were collected 

by the USGS during the fall of 1987 at 372 sites 

(fig. 6). Details about the sampling design are described in Colman and Sanzolone (1991). Of the 

372 streambed-sediment sampling sites, 238 were on 

low-order (first- and second-order) streams that were 

randomly selected from a grid (with grid-element sides 

of 6.2 mi) placed over a basin map. The remaining 

134 streambed-sediment sampling sites were on highorder (fourth-order or higher) streams. Data were 

available for all 22 elements discussed in this report. 

In addition, the samples also were analyzed for 

35 other elements including total carbon, inorganic 

carbon, major cations, and rare earth elements 

(Colman and Sanzolone, 1991). In 1990, streambedsediment samples were collected simultaneously with 

biota at the 25 tissue-sampling sites; however, lack of 

fine-grained sediments precluded element analysis at 

Mukwonago River (site 78) and Honey Creek 

(sites 80 and 81).

Samples of biological tissue were collected by 

the USGS at low streamflows at 15 and 25 sites during 

the summers of 1989 and 1990, respectively (fig. 5). 

Sampling locations for tissues were chosen on the 

basis of ecoregion (Omernik and Gallant, 1988), land 

use, historical data, and accessibility; sites included 

low- and high-order streams. To the extent possible, 

sites were coincident with fixed sites and streambed 

synoptic sites. Low-order stream sites included 

paired sites and other urban sites of interest. The 

paired sites were similar in size and drainage area to 

each other and were composed of one or more 

reference sites (sites selected to represent drainage 

basins that were either minimally affected or stable 

with regard to human activities) and one or more other

Design of the Illinois Environmental Protection Agency and National Water-Quality Assessment Programs for Major and Trace 17
sites selected to represent agricultural or urban land 

uses. At least one set of paired sites was sampled in 

each of the three ecoregions: Central Corn Belt 

Plains, Southeastern Wisconsin Till Plains, and 

Southern Michigan/Northern Indiana Till Plains. 

Reference sites sampled in the Central Corn Belt 

Plains, the largest ecoregion were Big Rock Creek 

(site 94), Indian Creek (site 97), Langan Creek 

(site 27), and Spring Creek (site 24); the Mukwonago 

River (site 78) and Mill Creek (site 2) were selected 

as reference sites in the Southeastern Wisconsin Till 

Plains and the Southern Michigan/Northern Indiana 

Till Plains, respectively.

Organisms collected for tissue analysis were 

selected from the list of national target organisms 

for the NAWQA program (Crawford and Luoma, 

1993). When organisms from the national target list 

could not be collected at a site, other organisms were 

substituted. The resulting mixture of tissue-sample 

types consisted of mollusks, fish livers, aquatic insects, 

aquatic plants, and crayfish. Of the 59 total samples 

analyzed in 1989 and 1990, 33 (56 percent) were fish 

livers. Of the 33 samples of fish livers collected, 23 

were from the common carp (Cyprinus carpio).

METHODS

Field and Laboratory Methods

Field and laboratory methods are briefly 

described below. Details about field and laboratory 

techniques can be found in the references listed in the 

following sections.

Water

Water samples were collected by the IEPA by 

use of equal width increments and equal transit rate 

(Illinois Environmental Protection Agency, 1987c). 

Water samples collected by the IEPA were analyzed 

at the IEPA Laboratories in Chicago and Champaign, 

111., for dissolved and total recoverable concentrations 

for 17 of the 22 elements. Samples analyzed for 

dissolved constituents had been passed through a 

0.45-(im-pore-size filter. Samples were preserved 

with nitric acid and digested with hydrochloric acid 

(Illinois Environmental Protection Agency, 1987d) 

(table Bl), except those analyzed for mercury. 

Laboratory methods include inductively coupled

plasma-atomic emission spectrometry, gas flame 

atomic absorption spectroscopy, direct atomic 

absorption, or atomic absorption spectroscopy 

(table B1). Minimum reporting levels are listed 

in Table Bl.

Water samples were also collected as part of the 

NAWQA program, again by use of equal width increments and equal transit rate (Sullivan and Blanchard, 

1994). Samples were analyzed by the IEPA laboratories listed above except that concentrations of dissolved antimony and molybdenum were determined by 

the USGS National Water-Quality Laboratory in 

Colorado (NWQL).

The NWQL periodically analyzed water 

samples to document discrepancies between the 

IEPA Laboratory and NWQL because of differences 

in analytical methods. Reported concentrations 

for both dissolved and total recoverable phases differ 

between the two laboratories from 0 to about 200 percent, neither laboratory reporting consistently larger 

or smaller values than the other (Troy Stinson, 

U.S. Geological Survey, oral commun., 1991). Thus, 

for consistency, only the results from IEPA laboratories are used in this report for the dissolved and 

total recoverable phases. Some samples were 

analyzed by the NWQL for quality assurance 

according to methods described by Fishman and 

Friedman (1989) and Mattraw and others (1989).

It must be mentioned here that a potential 

problem is, however, inherent in the interpretation 

of dissolved concentrations of certain trace elements. 

Recent studies indicate that the standard accepted protocol used by many agencies for collecting and analyzing trace element data, especially the dissolved 

component, results in higher potential for sample contamination than newer, ultraclean techniques 

do (Windom and others, 1991). Thus, in this 

report, results from the analyses of these dissolved

!Total recoverable concentration of an element in water is 

an operational definition and is dependent on the extraction method 

used to isolate the element (Horowitz, 1991). Comparison of 

total and dissolved element concentrations from different studies 

is difficult because of the different methods used for filtering, 

extraction, or identification. The dissolved phase of water is 

defined operationally as any substance that passes through a 

0.45-^im-pore-size filter (Hem, 1985). This phase includes small 

particulates such as metal hydroxides, aluminosilicates, and 

organic matter; colloids; and ions in solution. The operational 

definition was not a problem in this study because filtering 

methods were similar in the EEPA and NAWQA programs and 

only data from the IEPA laboratories were used in this report.

18 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
constituents are included, but discussion of the implications of the results is kept to a minimum because 

of the known potential problems with the data. 

Therefore, caution was used in the interpretation of the 

following dissolved constituents: arsenic, beryllium, 

cadmium, chromium, copper, lead, mercury, and zinc 

(D.A. Rickert, U.S. Geological Survey, written 

commun., 1991; Windom and others, 1991). The 

USGS also has reported that dissolved boron concentrations may reflect significant sample contamination 

(D.A. Rickert, U.S. Geological Survey, written 

commun., 1991).

Suspended and Streambed Sediment

Suspended-sediment samples were collected 

and analyzed by use of standard USGS equipment 

and procedures (Sullivan and Blanchard, 1994). 

Concentrations of suspended sediment and the 

percentage of suspended sediment in the fine 

fraction were determined by the USGS sediment 

laboratory in Iowa City, Iowa, by use of techniques 

described by Guy (1977). Sediment surface areas 

were determined by the USGS, Doraville, Ga., by 

use of the single point BET (Brunauer, Emmett, 

Teller) method with a mixture of 30 percent helium 

per 70 percent nitrogen gas (Horowitz and Elrick, 

1987); reporting units are in square meters per gram. 

Nondestructive surface-area-measurement techniques 

were used instead of grain-size analysis because 

of the small sample size of suspended sediment. 

Surface area is inversely related to grain size 

(Horowitz, 1991). Concentrations of trace 

elements in suspended sediment were determined 

by the USGS Geologic Division, Branch of 

Geochemistry, Menlo Park, Calif., according to 

methods described by Fishman and Friedman (1989) 

and are listed in table B1. Total digestions were 

used. Minimum reporting levels are given in 

table Bl.

Samples of streambed sediments collected by 

the IEPA were composite samples from the upper 

one-half inch of deposits, which consisted of formerly 

suspended materials (Illinois Environmental Protection 

Agency, 1987c). During the period of interest to this 

report, sieving practices changed. Approximately 

one-half of the samples are from unsieved samples 

of streambed sediments that were collected during 

1978-82. The remainder are from samples collected 

during 1982-87 and sieved wet (less than 63 (im). 

Background information on the sample collection

and analysis is sketchy; however, partial digestions are 

known to have been used in the chemical analysis. 

Sampling was repeated at some sites; only the data 

from the most recent sampling are used in this report. 

Streambed-sediment samples collected as part 

of the NAWQA program were composited from three 

to several subsamples from the oxic surface sediments 

(top 1 in.) at each site. High-order streams were 

sampled at 5-mi intervals in urban areas and at 10-mi 

intervals in agricultural areas. Methods of sampling 

and analysis were similar at sites on high- and loworder streams, except that sediments from high-order 

streams were sieved wet and sediments from low-order 

streams were sieved dry (Colman and Sanzolone,

1991).

A description of the methods used by the USGS 

to analyze for trace elements in streambed sediments 

and a listing of minimum reporting levels are given in 

table B1. Total digestions were used in the chemical 

analysis except for boron (Colman and Sanzolone,

1992). All reported concentrations are from the 

less-than-63-(im fraction (silt- and clay-size particles). 

No data are available for the proportion of the whole 

sample that was less than 63 (im in diameter.

Analysis of the variance between sieving methods used by the USGS at 22 sites indicated significant 

variations in median concentrations because of the 

sieving methods for most of the 48 elements surveyed 

(Colman and Sanzolone, 1992). For most elements, 

including the priority pollutants, concentrations from 

wet-sieved sediments were larger than from dry-sieved 

sediments. Only mercury concentrations were larger 

in dry-sieved sediments than in wet-sieved sediments 

(Colman and Sanzolone, 1992).

Biota

Tissue samples for the analysis of trace elements were collected from 15 sites in 1989 and from 

25 sites in 1990 according to field methods described 

in Crawford and Luoma (1993). Additional water 

samples were collected near the time of biological 

sampling at sites that were not part of the fixed-site 

sampling.

Mollusks were collected from four sites in 1989 

and six sites in 1990 by hand gathering or by use of a 

clam rake. Each sample from a site was a composite 

of at least three individuals and, at all but two sites, 

was composed of individuals of a single species. 

Individuals were rinsed with deionized water and 

scrubbed with a soft nylon-bristle brush to remove

Methods 19
attached particles. Mollusks were then held in polyethylene aquariums containing deionized water at 

10°C for a 48-hour depuration period to allow sediment and other material to pass through the gut. 

Water in the aquariums was replaced every 24 hours. 

After the depuration period, shell length was measured 

as greatest anterior-posterior dimension. The soft 

tissue was removed from the shell by use of stainlesssteel scalpels that had been cleaned with nitric acid. 

Composite samples of soft tissues were placed in clean 

glass jars and frozen on dry ice for later analysis. 

Snails (Physella Integra) and fingernail clams 

(Musculium sp.) were collected at only one site each 

and, unlike other mollusks sampled, were analyzed 

with the shells included. Concentrations in these two 

samples, therefore, represent elements adsorbed to the 

shell as well as bioaccumulated elements incorporated 

into soft tissues. Elemental concentrations in these 

two samples should be interpreted with caution and 

should not be compared to concentrations in other 

mollusks from the basin.

Fish samples for tissue analyses were collected 

by electrofishing. Backpack electrofishing units 

were used in wadable streams and boat-mounted units 

were used for nonwadable streams. In accordance 

with the sampling strategy for NAWQA (Crawford 

and Luoma, 1993), fish livers were extracted and 

composited for the analysis of trace elements. Each 

sample from a site consisted of a composite of 3 to 

10 fish livers from a single species. Fish during the 

sampling were sacrificed by a sharp blow to the base 

of the skull. Fish were then blotted with a lint-free 

cloth to remove excess moisture, were weighed, and 

were measured for total length. The liver of each fish 

was removed by use of a stainless-steel scalpel, was 

placed in a clean glass jar with a Teflon-lined cap, and 

was frozen on dry ice for later analysis.

Only one sample of aquatic insects was collected; this was a sample of caddisflies (Hydropsyche sp.) 

from Salt Creek in 1989. Caddisflies were collected 

by use of kick nets and by handpicking of organic 

debris. The sample consisted of a composite of 

approximately 260 individual larval caddisflies.

Once collected, the sample was rinsed three times 

with deionized water in an effort to remove attached 

particles. The composite sample of whole individuals was then placed in a clean glass jar and frozen 

on dry ice.

Crayfish were sampled during 1989 but not 

during 1990. Collection methods included use of

l/8-in.-mesh seines. Composite samples of crayfish 

consisted of 4 to 30 whole individuals. Collections 

were made without regard to species. Subsequent 

identifications showed that the samples included three 

species of the genus Orconectes: O. virilis, O. rusticus, and O. propinquus. Each sample was rinsed 

three times with deionized water to remove attached 

particles. Composite samples of whole individuals 

were then placed in clean glass jars and frozen on dry 

ice. No depuration period was allowed for crayfish.

Rooted aquatic plants were collected by hand 

picking of leaves and stems from the apical 2 in. of 

submersed plants by use of unpowdered vinyl gloves. 

Enough plant material was collected to provide at least 

25 g (wet weight) of material from a single species for 

each composite sample. The apical tissue was rinsed 

three times in deionized water, placed in a clean glass 

jar, and frozen on dry ice.

Laboratory methods for biota included homogenization followed by analysis of freeze-dried material. 

A nitric-perchloric acid decomposition method was 

used for all elements except mercury, for which nitric 

acid alone was used. Hydride generation atomic absorption spectrophotometry (AAS) was used for analysis of arsenic and selenium, and cold-vapor AAS was 

used for analysis of mercury. All other elements in 

biota were analyzed by means of inductively-coupled 

plasma emission spectroscopy (ICPES). Unless 

otherwise stated, element concentrations in biota are 

reported as micrograms per gram dry weight (DW). 

All laboratory analyses were done by the Environmental Trace Substances Laboratory, University of 

Missouri, Columbia, Mo. Quality-assurance methods 

for biota included blanks, duplicates, spikes, and 

reference standards (oyster tissue, bovine liver, and 

citrus leaves from the National Institute of Standards 

and Technology). Minimum reporting levels for 

elements in tissues of biota are listed in table Bl.

Statistical Methods

Numerous statistical techniques were used to 

analyze the data base that was compiled. This section 

provides a brief overview of these statistical 

procedures. Where possible, a reference is provided 

for a work that gives a more complete description of 

the statistical method and its application.

Water-quality data are typically highly skewed 

and not normally distributed. When a parametric 

statistical method is applied to this type of data, the

20 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
power of the method decreases, and the results may 

be in error (Helsel, 1987). Nonparametric statistics 

are more powerful tools for the analysis of highly 

skewed data and allow for successful analysis when 

normality cannot be assumed for all groups to be 

compared. Helsel (1987) examines these and other 

advantages of nonparametric statistics for the analysis 

of water-quality data. In light of the utility of nonparametric statistics for the analysis of water-quality 

data, nonparametric statistics were used primarily for 

the descriptive analyses of the data in this study.

Many sets of concentration data for dissolved or 

total recoverable elements in water are referred to as 

"censored" because some observations in the set are 

lower than limits deemed reliable enough to report as 

numerical values. These so-called less-than values 

are typically reported as "< rl" where rl is the 

minimum reporting level. The presence of less-than 

values in data sets with multiple reporting levels is a 

problem with many of the trace elements, especially 

the environmentally important priority pollutants 

arsenic, beryllium, cadmium, chromium, copper, lead, 

mercury, and zinc. Reporting levels for these constituents varied over time because different laboratories 

did the analyses, laboratory equipment improved, or 

analytical techniques changed. The number of lessthan values limits the usefulness of these data for 

statistical analysis and also for determining spatial 

distributions of trace elements across the basin. 

Because dissolved concentrations are usually smaller 

than total recoverable concentrations, fewer uncensored data are available for statistical analysis of the 

dissolved component. Unfortunately, the dissolved 

component is the most important phase for determining the bioavailability and toxicity of these 

elements to aquatic life. Statistical analyses of 

censored data required substitution of a numerical 

value for each less-than value. In general, zero was 

substituted for the less-than values; thus, all the lessthan values were tied for the lowest rank in the ranktransformed data set. Where different substitutions 

were used for a statistical test, they are discussed with 

the description of that test.

The first level of analysis was a general 

description of the temporal and spatial distributions 

of concentrations for each target element. Percentiles 

were used to classify different parts of the distribution 

for some components. The percentiles that are used 

to group data in this report are the 10th, 25th, 50th, 

75th, and 90th. The 50th percentile is the median,

or middle observation of the data when concentrations 

are ordered from smallest to largest. The 10th percentile is the concentration at which 10 percent of the 

measured concentrations are less than that value. 

Additional information on use of percentiles is 

presented by Iman and Conover (1983) and Kleiner 

and Graedel (1980). Statistics were computed for 

individual sites where at least 10 observations had 

been compiled for a given constituent. The 10th and 

90th percentiles were not computed for sites where 

less than 30 observations had been compiled for a 

given constituent during water years 1978-86. 

Percentiles for censored data with multiple reporting 

levels were reported as less than the maximum 

reporting level for all percentiles smaller than this 

concentration and reported as numerical values for 

concentrations greater than this level.

Tukey schematic plots were used to show the 

distribution of all the data values in figures A1-A3. 

A Tukey schematic plot is a modified box plot. 

Tukey schematic plots are further described by Tukey 

(1977).

Tukey plots for data sets with multiple reporting 

levels were modified to display quartiles estimated by 

fitting the data to a log-normal distribution by use of a 

procedure described by Helsel (1990). A carat symbol on the box plot represents the maximum reporting 

level. Any part of the box below the maximum 

reporting level was drawn using estimated values 

based on Helsel (1990) procedures. If the maximum 

reporting level was greater than the upper adjacent 

value, no upper whisker was drawn. If the maximum 

reporting level was greater than the 25th percentile, no 

lower whisker was drawn. If the maximum reporting 

level was less than the lower adjacent value, the lower 

whisker was not extended below the maximum reporting level. Outside and detached values that were less 

than the maximum reporting level cannot be estimated 

and were not plotted.

Water-quality criteria provided a reference to 

describe concentrations that are considered to be 

elevated. These comparisons are not intended to 

identify violations of water-quality standards; the 

criteria used, which in some cases are provisional, 

nonenforceable guidelines, are not necessarily those 

adopted by Illinois, Indiana, and Wisconsin, nor are 

they always directly applicable to the conditions 

sampled. The descriptive part of the data analysis 

also included identifying the number of observations 

that exceeded water-quality criteria for a given

Methods 21
constituent. In this report, the Federal water-quality 

criteria administered by the USEPA (U.S. Environmental Protection Agency, 1986) and 85- and 

95-percent Elevated Data Levels (EDL 85 and 95) 

from California's Toxic Substances Monitoring 

Program (TSMP) (Rasmussen, 1992) were used as the 

criteria for comparison unless otherwise noted. The 

reason these criteria were used is that the State criteria 

differ throughout the study area and have also been 

revised and updated over time. The use of the 

Federal criteria and TSMP EDL's provided a uniform 

set of criteria for comparison in the study area.

Concentrations of elements in sediment were 

log-transformed or standardized before graphical or 

statistical analyses. Statistical analyses of streambedsediment data collected from 1978 through 1986 were 

done on the base 10 logarithm of the concentrations 

(log-transformed data) rather than the untransformed 

data. Taking the logarithm transformed the skewed 

distribution of values to a normal distribution, which 

then could be analyzed by use of common parametric 

statistical tests. Details on log transformation of data 

are given in Iman and Conover (1983).

The second level of analyses was examination 

of differences and similarities among groups of data. 

These included differences among sites or river basins, 

differences between periods, and correlations among 

elements. For all statistical tests in this report, a 

significance probability (p-level) was computed. 

This p-level indicates the probability of erroneously 

reporting a trend when data values are random, 

independent, and identically distributed. Results 

were considered significant when p-levels were less 

than 0.10.

The Wilcoxon signed-ranks procedure was 

used to test for differences between dissolved and 

total recoverable concentration of some constituents. 

The Wilcoxon test is a nonparametric test that is 

similar to a t-test, except that the test is done on the 

signed ranks of the differences between paired data 

points. A detailed description of the Wilcoxon 

test is given by Iman and Conover (1983).

The Kruskal-Wallis test is a nonparametric 

analysis of variance (ANOVA) on rank-transformed 

data. This test indicates whether the variance among 

samples in a group (such as at a site, in a river basin, or 

by use of a certain method) is large enough to mask 

differences among the medians of the groups. Details 

about the Kruskal-Wallis test are given in Iman and 

Conover (1983). The Kruskal-Wallis test indicates

whether at least one group is distinguishable from the 

others. The Tukey studentized range test (Neter and 

others, 1985) was used to identify which groups from 

the Kruskal-Wallis test were similar to each other.

Plots of the percentage of samples with 

concentrations greater than a given value (probability plots) were used to describe differences among 

samples collected at different times and to delineate 

background from elevated concentrations. Rickert 

and others (1977) proposed that probability plots of 

background concentrations in the Willamette River 

in Oregon, would follow a curve with few breaks. 

Breaks in curves of probability plots represent the 

delineation between background and elevated concentrations.

Correlation coefficients were used to identify 

elements that behaved similarly among sites, among 

the different components sampled, or over time. 

Linear correlation coefficients, signified by r (Iman 

and Conover, 1983), were used to quantify the strength 

of the linear relations among log-transformed element 

concentrations in streambed sediment. Rank correlation coefficients, signified by Spearman's rho (p) 

(Johnson and Wichern, 1982; Iman and Conover, 

1983), were used to identify and group trace elements 

that significantly correlated with each other in water, 

sediment, and biota. Spearman's rho quantifies the 

strength of the monotonic relations among elements 

without requiring the relation to be linear. Spearman's rho also enables comparisons from censored 

data because ranks, rather than actual values, are 

used. For data sets containing multiple reporting 

levels, correlations were calculated twice first with 

less-than values set to zero and second with less-than 

values set to the reporting level thus, some correlation coefficients may be represented by two values. 

If the coefficients from either of the calculations was 

not significant (p < 0.1), neither coefficient was 

included in the tables or discussion. This procedure 

was especially important in correlating element 

concentrations in water because many of the elements 

were reported at multiple levels and correlation coefficients sometimes varied widely among the substituted 

values. Only correlations with p-levels less than 0.10 

and coefficients (p) greater than 0.5 were considered 

significant and are discussed. In addition, correlations among data sets in which greater than half of 

the observations that were below the reporting level 

were excluded. Correlations among sites were not

22 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
included in the tables and discussion if the data sets 

of interest were censored at more than 15 sites.

Factor analysis was used to summarize subsets 

of the water- and streambed-sediment-quality data by 

identifying groups of constituents that are highly correlated. Factor analysis is a technique that summarizes the variance-covariance or correlation structure 

of a data set by identifying major axes of variation 

within the data matrix (Davis, 1986). These axes, 

called principal components, are linear combinations 

of the original variables (Johnson and Wichern, 1982, 

p. 362). The first principal component expresses as 

much of the total system variability as can be explained by a single axis. Successive principal components each express part of the remaining variability 

and are uncorrelated to previously derived principal 

components. The degree of association between a 

variable and a principal component is expressed by a 

measure called the loading. Loadings reflect, ". . . the 

relative importance of a variable within a principal 

component, . . ."(Davis, 1986, p. 537). If a group of 

variables all load heavily on a particular principal 

component, then the variables all behave similarly. 

For example, if a group of elements all load heavily on 

a particular component, then all of those elements are 

likely to be associated with a common source, such as 

a particular soil type. Detailed discussions of factor 

analysis are found in Johnson and Wichern (1982), 

Pielou (1984), and Davis (1986).

The third level of analysis was examination of 

the transport of dissolved and suspended material past 

water-quality-monitoring sites. The instantaneous 

amount of material transported past a site, the load, 

can be calculated by multiplying the constituent 

concentration by the discharge. A regression model 

can be developed between the instantaneous load and 

functions of discharge and time. This regression 

model was used to estimate daily loads from the daily 

discharge record. The best-fit regression model is in 

the form

In(CQk) =

where

C is concentration, in milligrams

per liter; 

Q is discharge, in cubic feet per

second; 

k is units conversion factor,

0.002714;

In is natural logarithm; 

In (CQk) is natural logarithm of the load,

in tons per day;

t is time, in decimal years, using 

January 1,1978, as time = 0; 

TC is 3.1416, a constant used here 

to convert decimal time to 

radians; 

sin (2nt) + cos (2nt) is a factor to account for

seasonal variability; 

/ is the y-axis intercept; and 

a, b, c, d are regression equation 

coefficients.

The best combination of independent variables, 

based on Mallows C statistic (Mallows, 1964), was 

chosen as the best load-estimation model. The best 

model was applied to the daily discharges for water 

years 1987 through 1990. The model results in the 

calculated log of the load; the log of the load was 

detransformed and multiplied by the Duan smearing 

estimate (Duan, 1983), a bias-correction factor. The 

daily loads were summed and averaged to produce a 

mean annual load for water years 1987 through 1990. 

For data sets containing multiple reporting levels, 

loads were calculated twice first with less-than 

values set to zero and second with less-than values set 

to the reporting level thus, some loads may be represented by two values.

The fourth level of analysis was an examination 

of seasonality, trends, and long-term changes in concentration over time. The seasonal Kendall test for 

trend and the seasonal Kendall slope estimator as 

described by Hirsch and others (1982) and Hirsch and 

Slack (1984) were used. With this test, the effect of 

seasonal variation is accounted for by comparing 

observations from the same season of the year. 

Twelve seasons per year were used for this investigation. Trend analyses were not done for sites 

where data sets consisted of less than 30 data values, 

less than 3 years of data, or a majority of less-than 

values. For data sets containing multiple reporting 

levels, trends were calculated twice first with lessthan values set to zero and second with less-than 

values set to the reporting level thus, some trends 

may be represented by two values. The trend results 

were included in the tables and discussion only if the 

results of the two sets of calculations both indicated 

significant trends in the same direction.

Kendall's tau is an equivalent measure to 

the rank correlation coefficient (Spearman's rho).

Methods 23
Tail measures the strength of the monotonic relation 

between two values and the general increase or 

decrease in the data regardless of whether the increase 

or decrease is linear. The seasonal Kendall slope 

estimate estimates the yearly change in the concentration of the constituent. It is calculated by dividing 

the differences between data values in the same season 

by the time between the values and then taking the 

median of all these values.

These procedures determined the presence of a 

trend and its magnitude. The application of these 

procedures to water-quality data on a national level is 

described by Smith and others (1987).

MAJOR AND TRACE ELEMENTS IN 

WATER, SEDIMENT, AND BIOTA

Element concentrations in water, sediment, and 

biota were compared among sites in the upper Illinois 

River Basin for a period before the NAWQA program 

(water and sediment only, from 1978 through 1986) 

and a period during the pilot NAWQA program (from 

1987 through 1990). Dissolved and total recoverable 

concentrations in water and suspended sediment were 

analyzed for seasonal variations. Analysis for trends 

in dissolved and total recoverable concentrations in 

water were done for the period 1978 through 1990. 

Correlations of element concentrations with concentrations of other elements were examined within water, 

sediment, and biotic components. Finally, correlations among elements in water, sediment, and biota 

also were examined. Site numbers in parentheses 

after site names are referenced in table 6 and figure 5.

Water

This description of trace elements in water is 

based on dissolved and total recoverable element 

concentrations in water samples collected from 1978 

through 1986 at the 38 sites in the IEPA Ambient 

Water-Quality Monitoring Network and collected from 

1987 through 1990 at a combination of EEPA and 

NAWQA fixed sites (fig. 5).

Results of Water-Data Collection, 1978-86

By Charles G. Crawford and Daniel J. Sullivan

Historical data for dissolved and total recoverable element concentrations in water were limited to

the 38 sites sampled by IEPA as part of the Ambient 

Water-Quality Monitoring Network (fig. 5). Data 

were available for most of the 22 elements except 

antimony, molybdenum, and selenium. No data were 

available for dissolved arsenic and mercury. The 

number of observations and the period of record for 

each element is variable among elements; however, 

data were generally collected at most sites from 1978 

through 1986 every 6 weeks.

Median concentrations of several of the major 

and trace elements were below the minimum reporting 

level. These elements were beryllium, cadmium, 

cobalt, lead, silver, and vanadium. In several 

individual samples, however, concentrations of 

cadmium, lead, and silver exceeded USEPA waterquality criteria.

Sites where total recoverable element concentrations exceeded USEPA freshwater chronic or acute 

criteria one or more times are listed in table 7. Sites 

where concentrations of several priority pollutants 

frequently exceeded USEPA water-quality criteria 

include the Des Plaines River near Gurnee (site 33), 

North Branch Chicago River at Niles (site 45), 

Addison Creek at Bellwood (site 39), Chicago Sanitary 

and Ship Canal at Lockport (site 56), West Branch 

Du Page River near Warrenville (site 64), and Illinois 

River at Marseilles (site 76). All of these sites except 

the Des Plaines River near Gurnee and the Illinois 

River at Marseilles are in highly populated areas that 

presently receive or historically received inputs from 

industrial and municipal sources. The Des Plaines 

River near Gurnee predominantly drains agricultural 

land. The Illinois River at Marseilles receives input 

from all sources in the basin except those in the Fox 

River. Concentrations of chromium, copper, lead, 

mercury, and zinc that exceeded USEPA freshwater 

chronic criteria were observed most frequently in the 

Des Plaines River Basin, an indication of the effects of 

urbanization in this basin. Concentrations of iron that 

exceeded USEPA freshwater chronic criteria for iron 

were evenly distributed across the upper Illinois River 

Basin.

Dissolved and total recoverable concentrations 

of most of the priority pollutants were largest in urban 

land-use areas. The spatial distribution of the median 

concentration of total recoverable copper (fig. 7) illustrates this pattern of urban effect. Median concentrations of total recoverable copper are largest at 

sites in the highly populated areas of the Des Plaines 

and Du Page River Basins and at sites downstream

24 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
EXPLANATION

UPPER ILLINOIS RIVER 

BASIN BOUNDARY

SAMPLING SITE - Number is 

median concentration of 

total recoverable copper, 

in micrograms per liter

LAKE MICHIGAN

Base from U.S. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic Projection

Standard parallels 33° and 45°, central meridian -89° 40 KILOMETERS

Figure 7. Median concentrations of total recoverable copper in the upper Illinois River Basin, 1978-86.

Major and Trace Elements in Water, Sediment, and Biota 25
from these areas. The sites where total recoverable 

copper concentrations are largest include Salt Creek at 

Western Springs (site 38), Des Plaines River at 

Lockport (site 42), and downstream at Illinois River 

at Marseilles (site 76). By contrast, median concentrations were 4.5 to 18 times smaller in the Fox, 

Kankakee, and Iroquois River Basins. The sites 

where total recoverable copper concentrations are 

largest and sites near them had the largest median 

concentrations of many of the elements, including 

dissolved and total recoverable boron, chromium, 

nickel, and strontium; total recoverable arsenic; and 

total recoverable zinc. Other urban sites with consistently larger median concentrations of many elements 

include the Des Plaines River near Schiller Park 

(site 35), Addison Creek at Bellwood (site 39), and 

the Calumet Sag Channel at Sag Bridge (site 54). 

The source of the elevated levels of these elements in 

the urban areas is likely a combination of industrial 

and municipal effluent, as well as runoff.

In contrast, median concentrations of some 

elements were larger in samples from the Fox, 

Kankakee, and Iroquois River Basins than in samples 

from the urbanized sites in the Des Plaines and 

Du Page River Basins. Median total recoverable 

concentrations of the soil-associated elements 

aluminum, iron, and manganese were largest in the 

Kankakee and Iroquois River Basins, where agriculture is the dominant land use. Large median 

concentrations of total recoverable aluminum (fig. 8), 

iron, and manganese in these agricultural basins are 

generally associated with agricultural practices, 

which cause increased erosion and increased solidphase concentrations of soil-related elements. 

Dissolved concentrations of these elements, however, 

did not form the same patterns as the total recoverable 

concentrations. Median dissolved iron and manganese concentrations were larger in urban areas, 

whereas median dissolved aluminium concentrations 

were similar at sites across the basin. This overall 

pattern indicates that the cause of the larger concentrations in the soil-related elements in agricultural areas 

was the particulate, or solid-phase fraction. Overall, 

total concentrations of the soil-related elements were 

more evenly distributed across the entire upper Illinois 

River Basin than other elements.

Variability in concentrations over the sampling 

period from any one site is generally greatest in urban 

areas. Solute concentrations in nonurban areas are 

not as likely to show the variability observed in urban

streams. Nonurban areas are not as strongly affected 

by the spontaneity of storms and fluctuations in contributions of elements from point sources that may exist 

in urban drainages.

An analysis of the loads and yields further 

indicated the effect of urbanization and industrialization on the concentrations of major metals and trace 

elements in the upper Illinois River Basin. For most 

of the elements identified urban related, yields were 

considerably larger from urban areas than from agricultural areas. As an example, yields of total boron 

were 2 to 13 times greater from urban areas than from 

agricultural areas (fig. 9).

In conclusion, the largest concentrations and 

yields of most metals and trace elements were 

observed in urban areas. Total recoverable concentrations of soil-associated elements were slightly 

elevated in agricultural areas. The USEPA freshwater chronic and acute water-quality criteria were 

exceeded in a large number of samples collected from 

1978 through 1986.

Results of Water-Data Collection, 1987-90

Data from analysis of trace elements in 

water (dissolved and total recoverable) from the 

eight NAWQA fixed stations are given in Sullivan 

and Blanchard (1994). Data from analysis of trace 

elements in water (dissolved and total recoverable) 

from the 8 NAWQA fixed stations and the 32 additional stations operated by the IEPA are given in 

USGS annual data reports (Fitzgerald and others, 

1988; Coupe and others, 1989; Sullivan and others, 

1990; Richards and others, 1991,1992). Boxplots for 

dissolved and total recoverable concentrations in water 

from 1987 through 1990 are shown in figures Al and 

A2, respectively.

As in the 1978-86 data, median concentrations 

of several elements were below or near the minimum 

reporting level (figs. Al and A2), including dissolved 

aluminum, dissolved antimony, dissolved and total 

arsenic, dissolved cadmium, dissolved and total recoverable lead, dissolved and total selenium, dissolved 

and total recoverable vanadium, and dissolved and 

total recoverable zinc.

Results from Kruskal-Wallis analysis of 

variance tests indicate that concentrations of dissolved 

and total recoverable beryllium, dissolved chromium, 

dissolved and total recoverable cobalt, dissolved 

copper, dissolved iron, dissolved and total recoverable

26 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
89°

43C

42C

41'

380

87° 86°

EXPLANATION

UPPER ILLINOIS RIVER 

BASIN BOUNDARY

SAMPLING SITE - Number is 

median concentration of 

total recoverable aluminum, 

in micrograms per liter

S^so -^e^pj

t C j«22P \ 470-.Il 

. .^\ 32^ ^510 \ j >0 >

LAKE MICHIGAN

Base from U.S. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic Projection

Standard parallels 33° and 45°, central meridian -89

40 MILES

n r

20 40 KILOMETERS

Figure 8. Median concentrations of total recoverable aluminum in the upper Illinois River Basin, 1978-86.

Major and Trace Elements in Water, Sediment, and Biota 27
Base from U.S. Geological Survey

1:100,000 Digital Line Graphs

Albers Equal-Area Conic Projection

Standard parallels 33° and 45°, central meridian -89° 20 40 KILOMETERS

Figure 9. Mean annual yields of total recoverable boron in the upper Illinois River Basin, 1978-86.

28 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
mercury, and dissolved and total recoverable silver 

were not significantly different (a = 0.5, p > 0.001) 

among sites across the basin. The lack of differences 

of these element concentrations among sites may be 

due to the large number of less-than values for these 

elements.

Of the 13 elements for which acute and chronic 

water-quality criteria have been established for total 

recoverable concentrations (table 4), 8 elements were 

present at concentrations greater than acute, chronic, 

or both criteria: cadmium, chromium, copper, iron, 

lead, mercury, silver, and zinc. These elements were 

the same as those that exceeded the criteria from 1978 

through 1986. The criteria were exceeded at approximately the same number of sites from 1978 through 

1986 as from 1987 through 1990, and about the same 

proportion of concentrations exceeded acute and 

chronic criteria at individual sites. For example, 

at the Illinois River at Marseilles (site 76), 18 and 

8 observations out of 80 samples collected by the 

IEPA from 1978 through 1986 exceeded the chronic 

and acute criteria for copper (table 7), and 11 and 

4 observations out of 62 samples collected as part of 

the NAWQA program from 1987 through 1990 

exceeded the chronic and acute criteria for copper.

All antimony, arsenic, beryllium, nickel, and 

selenium concentrations were below acute and chronic 

criteria at all sites from 1978 through 1990.

Dissolved and total recoverable concentrations 

of most major metals and trace elements, including 

many elements that are considered priority pollutants 

(table 4), were largest in urban land-use areas. In the 

upper Illinois River Basin, these elements include boron, cadmium, chromium, copper, lead, molybdenum, 

nickel, and zinc. These elements are referred to as 

"urban-related elements" in the following sections. 

Spatial patterns of total recoverable concentrations of 

antimony, arsenic, beryllium, mercury, selenium, and 

silver could not be related to land use because the large 

number of less-than values at agricultural and urban 

sites.

Concentrations of aluminum, iron, manganese, 

and vanadium in water did not coincide with any 

particular land use. These elements are typically 

considered soil-related elements and are common 

constituents in silt and clay. Thus, many agricultural 

streams that have an abundance of fine-grained 

sediment in their basins and are intensively farmed 

contain large total recoverable concentrations of 

these elements. Dissolved concentrations of these

elements in the same streams usually are below the 

minimum reporting level. At many urban sites, 

however, the large concentrations of dissolved 

aluminum, iron, and manganese indicate contributions 

of these elements from point sources such as metalmanufacturing industries. Therefore, large total 

recoverable concentrations of these elements may be 

due to either a large dissolved component from urban 

areas or a large particulate component from soils.

Large concentrations of barium and strontium in 

stream water from the Fox and Du Page Rivers appear 

to be linked with ground-water contributions and 

carbonate bedrock. In many public water-supply 

wells in Kane and Du Page Counties, ground water 

from the Cambrian and Ordovician aquifers contains 

dissolved barium concentrations that exceed 10 mg/L 

(Gilkeson and others, 1983). Water from many wells 

in eastern Wisconsin, especially Waukesha County, 

has greater than 1 mg/L strontium (Hem, 1985). 

Barium is not removed by conventional water- or 

waste water-treatment methods; thus, concentrations 

of barium in the ground water may remain the same as 

the water is treated and used, unlike strontium, and 

discharged into the streams. Lime softening with 

soda-ash addition can remove approximately 90 percent of strontium (U.S. Environmental Protection 

Agency, 1991). Veins in carbonate rocks in this area 

may contain strontium-bearing minerals which may be 

mobilized under oxidized conditions when in contact 

with stream water (Brown and Maass, 1994). Even 

though concentrations of strontium are larger in the 

Fox and Du Page Rivers than in the rest of the streams 

in the upper Illinois River Basin, they are still within 

background concentrations found in rocks, soils, 

and surficial deposits (table 1).

Sites that receive large contributions of water 

from Lake Michigan (sites 54 and 55) contain some 

elements in concentrations that are more typical of 

water from a lacustrine environment than an urban 

riverine environment. For example, total recoverable 

barium concentrations are smaller at these sites (about 

15 to 30 |lg/L) than at other sites in the basin (about 

25 to 100 |lg/L). Lake Michigan water has concentrations of barium that range from 14 to 23 |lg/L near 

the water intakes for the city (City of Chicago and 

Illinois Environmental Protection Agency, 1989). In 

contrast, the median concentration for barium in public 

water supplies is 43 |lg/L, and from large rivers in the 

Nation is 45 |lg/L (Hem, 1985). Other concentrations 

that are much lower in Lake Michigan water than

Major and Trace Elements in Water, Sediment, and Biota 29
stream water in the upper Illinois River Basin include 

aluminum, boron, iron, manganese, and strontium 

(City of Chicago and Illinois Environmental Protection 

Agency, 1989). Except for boron, these elements are 

related to sources such as soils and ground water.

Mean annual loads and yields (table A4) of the 

urban-related elements at urban sites typically were 

one order of magnitude larger than loads and yields of 

the same elements from agricultural areas. Mean 

annual loads and yields for water years 1987 through 

1990 were calculated on the basis of total recoverable 

concentrations of elements at the 8 NAWQA fixed 

stations and at 18 additional IEPA stations for which 

streamflow data were available. For example, mean 

annual yields of lead and zinc from the Chicago 

Sanitary and Ship Canal at Romeoville (site 55) were 

about 0.065 ton/mi2 and about 0.45 ton/mi2, respectively (table 8). In contrast, yields of lead and zinc 

from the Iroquois River near Chebanse (site 28), 

a more agricultural stream, were 0.005 ton/mi2 and 

about 0.01 tons/mi , respectively. At sites even more 

agricultural than the Iroquois River near Chebanse 

(such as Sugar Creek at Milford, site 22), too many 

values were below the minimum reporting levels for 

loads and yields of these urban-related elements to be 

adequately calculated.

Atmospheric loading has been shown to 

contribute significant amounts of some trace elements 

to Lake Michigan (Eisenreich, 1980). Atmospheric 

loadings estimated for southern Lake Michigan by 

Eisenreich (1980) were converted to yields and 

compared to yields from four urban streams in the 

Chicago area and one agricultural stream (table 8). 

Streams in the Chicago area were selected because 

Gatz and others (1988) showed that element concentrations in atmospheric deposition are larger southeast of 

Chicago and in northern Indiana and are smaller in the 

western suburbs of Chicago. This pattern in atmospheric deposition probably is because of the prevailing 

westerly winds that move the airborne elements 

eastward and out of the basin (Peters and Bonelli, 

1982).

Some yields of urban- and industrial-related elements from atmospheric deposition were similar 

to yields from streams but others are not (table 8). 

Yields of lead in atmospheric deposition were very 

similar to those in streams in the Chicago area. A 

56-percent reduction in the use of lead in gasoline 

from 1979 to 1983 resulted in decreases in atmospheric fluxes of lead (Eisenreich and others, 1986).

Yields of lead from streams and atmospheric deposition in the Chicago area were similar. This similarity 

indicates that much of the lead in streams is derived 

from atmospheric deposition in the Chicago area. 

Yields from the Iroquois River were an order of 

magnitude less than from streams and atmospheric 

deposition in the Chicago area. Much larger yields 

of copper and zinc were observed in streams in the 

Chicago area than in atmospheric deposition. This 

pattern indicates that the main source of copper and 

zinc is not from atmospheric deposition but from 

urban runoff, as found by Striegl and Cowan (1987), 

or from point sources. As can be seen in table 8, 

the yield of copper in water from the Iroquois River 

is similar to the yield of copper in atmospheric deposition. Because copper is not a common element in 

geologic deposits in the Iroquois River Basin and 

urban runoff and point sources are not common, this 

similarly indicates that most of the copper in agricultural streams is derived from atmospheric deposition. 

Comparison of results from this study to results 

from other studies is of little help in determining 

whether concentrations in the upper Illinois River 

Basin are elevated or within background concentrations, because of differences in collection methods, 

sample processing and analyzing, and minimum 

reporting levels (Harmeson and Larson, 1969; 

Williams and others, 1974, p. 86; Feder, 1979; Kelly 

and Hite, 1981; Britton and others, 1983; City of 

Chicago and Illinois Environmental Protection 

Agency, 1985; Hem, 1985; Smith and others, 1987; 

Striegl and Cowan, 1987). In addition, many data 

for water are from the dissolved fraction and not 

highly reliable for the trace elements because of small 

concentrations. Thus, comparisons between studies 

can only be considered as highly general. Given 

those limitations, total recoverable concentrations of 

aluminum, arsenic, beryllium, cobalt, manganese, 

selenium, and vanadium all generally seem to be 

within background concentrations (table 1), although 

comparisons are inconclusive for beryllium, cobalt, 

and selenium because of too many less-than values. 

Some total recoverable concentrations of cadmium, 

chromium, copper, lead, mercury, nickel, silver, and 

zinc seem to be elevated in urban areas. An exact 

concentration that separates background from elevated 

concentrations in water cannot be identified; however, 

all elements whose concentrations exceed waterquality criteria (cadmium, chromium, copper, iron, 

lead, mercury, silver, and zinc) can be considered to

30 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
be elevated in the upper Illinois River Basin. Iron is 

the only one of these elements whose elevated concentrations in the upper Illinois River Basin does not seem 

to be related to urban sources.

Correlations Among Major and Trace Elements in 

Water, 1987-90

Dissolved and total recoverable concentrations 

of the 22 elements of interest at 40 sites (8 NAWQA 

fixed sites and 32 IEPA Ambient Water-Quality 

Monitoring Network sites) were correlated and a suite 

of other chemical constituents including dissolved and 

total recoverable concentrations of major ions, 

chloride, dissolved solids, suspended solids, volatile 

suspended solids, and total organic carbon; and with 

measurements of discharge, specific conductance, pH, 

water temperature, dissolved oxygen, alkalinity, and 

hardness.

Correlation coefficients (Spearman's rho) were 

computed from ranked data sets in three different 

ways. First, the data from the 40 sites were combined 

to find correlations that best describe basinwide correlations on main stems in the upper Illinois River 

Basin. Next, data were limited to dissolved and total 

recoverable concentrations from the eight NAWQA 

fixed sites. Finally, correlations among constituents 

were examined separately at each of the eight 

NAWQA fixed sites to distinguish the variation in 

correlation patterns in water for each individual 

site. Results of the correlation analysis for the 

40 sites combined, the 8 NAWQA fixed sites combined, and each individual NAWQA fixed site, are 

listed in table 9. Except for a few elements, the 

correlation results from the 40 sites and the 8 sites 

combined were similar.

Comparison of the correlation coefficients for 

the eight individual NAWQA fixed sites indicates that 

significant correlations among dissolved and total 

recoverable concentrations were not only element 

specific, but commonly site specific as well. These 

correlations reflect, in part, the site dependency of the 

partitioning of the element between the dissolved and 

particulate phases. If much of the element is in the 

dissolved phase, the dependence of the total recoverable concentration on the dissolved concentration 

increases, and, therefore, the correlation coefficient 

increases.

Large correlation coefficients for dissolved and 

total recoverable arsenic, barium, boron, and strontium

at the combined 40 sites and the combined 8 NAWQA 

fixed sites indicate that these elements were found 

mainly in the dissolved phase in water in the upper 

Illinois River Basin. Box plots of these elements 

(figs. Al and A2) show the relation between dissolved 

and total recoverable concentrations. In particular, 

correlation coefficients for dissolved and total recoverable boron and strontium concentrations were greater 

than 0.94 at each of the eight NAWQA fixed sites; 

other studies have shown that, in river transport, ratios 

of dissolved to total strontium and boron are high 

(Meybeck and Helmer, 1989).

Correlation analyses indicated that relations 

between dissolved and total recoverable concentrations 

of some elements varied between sites, whereas no 

relations were observed for other sites. Dissolved 

and total recoverable concentrations of arsenic, 

barium, and nickel correlated at some of the eight 

NAWQA fixed sites (p > 0.5) but not at all sites. 

This finding indicates that ratios of dissolved to total 

arsenic, barium, and nickel were site dependent; 

however, the correlations of dissolved to total recoverable concentrations were not dependent on land use 

because the coefficients were not consistent at sites 

with similar land use upstream. Dissolved and total 

recoverable phases did not correlate strongly at any of 

the sites for the elements aluminum, copper, iron, and 

lead; this finding indicates that these elements are 

mainly bound to the particulate phase or that the 

relation between the phases is variable. Dissolved 

and total recoverable manganese concentrations correlated strongly only at the Chicago Sanitary and Ship 

Canal (site 55). The variation in the pattern of box 

plots for all 40 sites for dissolved and total recoverable 

manganese (figs. Al and A2) indicates the wide range 

in the proportions of manganese in the dissolved and 

particulate phases.

Total recoverable concentrations of aluminum 

and iron (fig. 10) were the only elements that were 

highly correlated at all 40 sites. Correlation coefficients between the two elements range from 0.8 at the 

Chicago Sanitary and Ship Canal (site 55) to 0.99 at 

the Iroquois River (site 28).

Total recoverable iron and manganese also 

correlated, although the correlation coefficients are 

somewhat smaller and cover a broader range 0.48 

at the Des Plaines River at Riverside (site 40) to 0.90 

at the Du Page River at Shorewood (site 69) than 

those for iron and aluminum. The broader range in

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SHIP CANAL AT ROMEOVILLE, ILLINOIS

SITE 28, IROQUOIS RIVER 

NEAR CHEBANSE, ILLINOIS

TOTAL RECOVERABLE ALUMINUM, 

IN MICROGRAMS PER LITER

Figure 10. Total recoverable aluminum and iron concentrations in the upper Illinois River Basin, 1987-90. 

(Site numbers refer to table 6.)

32 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
correlation coefficients across the eight NAWQA sites 

reflects the site dependence of dissolved manganese 

concentrations.

Total recoverable manganese concentrations 

also correlated to total recoverable aluminum concentrations in a similar way as they did to iron; the 

smallest correlation coefficients (0.48 and 0.24) at 

the Des Plaines River (site 40) and Chicago Sanitary 

and Ship Canal (site 55), respectively, and the largest 

(0.86) at the Du Page River (site 69).

Total recoverable iron, aluminum, and manganese all positively correlated with total recoverable 

arsenic and barium, suspended residue, and volatile 

suspended residue, and negatively correlated with 

hardness and dissolved calcium concentrations at four 

to six of the eight NAWQA fixed sites. Total recoverable arsenic and manganese correlated with each 

other at the Kankakee River (site 14), the Iroquois 

River (site 28), and the two sites on the Fox River 

(sites 89 and 99). Dissolved and total arsenic also 

strongly correlated with water temperature.

Dissolved and total recoverable boron and 

strontium also correlated with each other at four to 

five of the eight NAWQA fixed sites; all four concentrations positively correlated with dissolved and total 

recoverable sodium, and dissolved chloride. They 

inversely correlated with discharge. This pattern 

further indicates that the dissolved concentrations of 

boron and strontium are diluted during high streamflow and are concentrated during low streamflow.

None of the other elements consistently correlated with any other elements, chemical constituents, 

or physical parameters. Cadmium is commonly 

associated with lead and zinc (City of Chicago and 

Illinois Environmental Protection Agency, 1985); 

however, cadmium did not correlate with lead or zinc 

at any sites. Cadmium may be coprecipitated with 

manganese oxides or adsorbed onto mineral surfaces 

(Hem, 1985); however, cadmium did not correlate 

with manganese or iron at any sites.

In water, nickel tends to coprecipitate with 

iron oxides and especially with manganese oxides 

(Salomons and Forstner, 1984). Nickel did not 

correlate with iron or manganese at any sites in the 

upper Illinois River Basin; however, it did inversely 

correlate with alkalinity at the eight NAWQA fixed 

sites combined and at the Illinois River at Marseilles 

(site 76).

Striegl and Cowan (1987) observed strong 

correlations among copper, lead, and zinc, and

suspended-sediment concentrations from Lake Ellyn in 

Illinois. Similar correlations were not apparent in the 

NAWQA data; correlations among copper, lead, 

and zinc and total suspended solids were negligible 

(table 9). Instead, only total recoverable aluminum, 

iron, and manganese significantly correlated with total 

suspended solids.

Chromium, copper, lead, and nickel inversely 

correlated with alkalinity among the combined data 

and at some of the eight NAWQA fixed sites. Hence, 

increased alkalinity (or carbonate) is linked to reduced 

concentrations of these metals. Water-quality criteria 

for all these metals are dependent on hardness (thus 

indirectly on alkalinity) (table 4). The relatively 

large alkalinity in the upper Illinois River Basin helps 

stabilize pH; therefore, pH probably does not vary 

enough to affect the speciation of these metals. Even 

though changes in pH are known to affect the distribution of metals over the dissolved and particulate 

phases, the buffering capacity of the water is usually a 

more important control, especially in systems where 

fluctuations in pH are small (Salomons and Forstner, 

1984). Thus, in the upper Illinois River Basin, 

alkalinity may be an important control on limiting the 

bioavailability of these metals.

Seasonal Variations and Long-Term Changes, 

1978-90

Data used for the analysis of seasonal variations 

in concentrations of elements in water include observations from the 40IEPA and USGS water-sampling 

sites. Data from 1978 through 1990 from ffiPA's 

38 ambient water-quality monitoring sites also were 

examined to determine if extension of the period from 

4 to 13 years changed the results of the analysis. The 

results from the comparison showed that the variations 

in median concentrations from month to month were 

the same, regardless of the period used; therefore, only 

the 1987 through 1990 data are discussed in this 

report. The seasonal variations discussed below are 

based on aggregated data for the 8 NAWQA fixed sites 

and the 32 IEPA monitoring sites.

Significant seasonal variations were observed 

in total recoverable concentrations of aluminum, 

arsenic, barium, boron, iron, manganese, and strontium in water (Kruskal-Wallis ANOVA, p < 0.10). 

Seasonal variations may occur in other trace element 

concentrations; however, too many observations of 

most of these elements are below the minimum 

reporting levels for variations to be statistically

Water 33
significant. Total recoverable aluminum, arsenic, 

iron, and manganese concentrations all varied 

similarly from month to month, with the largest 

concentrations occurring in the summer (fig. 11). 

These seasonal variations relate to seasonal variations 

in volatile and total suspended solids concentrations 

(fig. 11) and possibly reflect the amount of water 

available for dilution or the amount of suspended 

sediment in the water column. Dissolved manganese 

varied differently from month to month than total 

recoverable manganese. Largest dissolved 

manganese concentrations occurred in January through 

March, and smallest concentrations in July and September. Hydrogen-ion activity was smallest in 

February and March but largest in October and 

November; thus, some factor in addition to pH may 

have been affecting dissolved manganese concentrations.

Seasonal variations in dissolved and total recoverable strontium concentrations reflect variations in 

streamflow. Concentrations of dissolved and total 

recoverable strontium were largest in the summer 

and fall, and smallest in April, May, and December. 

These variations, which seem to be inversely related to 

streamflow, were largest in April, May, and December 

(fig. 12). Monthly boron concentrations also seem to 

be somewhat inversely related to streamflow, except in 

March and April (fig. 12). This is probably because 

of the effects of dilution of the elements at high flows. 

As mentioned previously, strontium in surface water is 

mainly from ground-water sources, and boron is 

probably from effluent from wastewater-treatment 

plants. When base flow contributes the most to 

overall streamflow, strontium and boron concentrations will be the largest.

Seasonal patterns in element concentrations 

varied from site to site. Seasonal variations in 

elements in water at the 40 sites combined were compared to individual seasonal variations at each of the 

eight NAWQA fixed sites. The seasonal patterns 

of aluminum, cadmium, chromium, cobalt, copper, 

nickel, vanadium, and zinc in water were variable at 

the eight NAWQA fixed sites; thus, it seems that 

seasonal variations of these elements in water were 

not caused by basinwide factors but by site-specific 

factors that may include geochemical substrate and 

biological processes. This finding is supported by 

other studies that have shown different monthly variations of element concentrations in water from the 

middle Illinois River (Mathis and Cummings, 1970).

Trends in element concentrations in water from 

1978 through 1990 were examined by use of seasonal 

Kendall analysis for 38 of the 40 sites sampled for 

water. The exact sampling periods differed among 

the sites but at least 9 years of data were available for 

most sites and as much as 13 years of data were 

available for some sites. The sampling period at the 

other two sites, the Des Plaines River (site 40) and the 

Chicago Sanitary and Ship Canal (site 55), was not 

long enough for trend analysis.

Results of the trend tests are given in table A5. 

Results are not included for sites where more than half 

of the observations were below the minimum reporting 

level. If less-than values were present, the trend tests 

were run twice once with zero substituted for the 

less-than values and once with minimum reporting 

levels substituted for the less-than values. If the trend 

results differed between the two tests, the results were 

not included, and only trends with a significant probability level (p < 0.10) are reported. Elements that 

were not analyzed for trends include the priority 

pollutants antimony, beryllium, mercury, silver, and 

zinc. Trend analysis of antimony concentrations 

were not possible because samples for antimony 

analysis were collected only during the NAWQA pilot 

study. More than half of the concentrations of 

beryllium, mercury, silver, and zinc were below the 

minimum reporting level at all sites, and many data 

sets for these elements contained multiple minimum 

reporting levels as well.

The number of sites where upward and 

downward trends were found for each element are 

listed in table 10. Concentrations of five elements 

had significant downward trends at a number of sites 

in the basin: dissolved and total recoverable barium 

(12 and 17 sites, respectively), total recoverable boron 

(13 sites), total recoverable iron (8 sites), dissolved 

and total recoverable manganese (13 and 14 sites, 

respectively), and dissolved and total recoverable 

strontium (7 and 6 sites, respectively). Dissolved and 

total strontium concentrations also had significant 

upward trends at many sites in the upper Illinois River 

Basin (9 and 15 sites, respectively). Plots of barium 

and boron at Salt Creek (site 38) and Thorn Creek 

(site 50) show the downward trends in these concentrations (fig. 13).

Sites where significant downward trends 

in barium were found were scattered across the 

Des Plaines, Du Page, and Fox River Basins; 

although these sites are mainly urban, a few

34 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
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volatile and total suspended solids in the upper Illinois River Basin, 1987-90.

Water 35
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upper Illinois River Basin, 1987-90.

36 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
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agricultural sites are included. Downward trends in 

boron were found at urban sites in the Des Plaines and 

Du Page River Basins. Downward trends in iron 

concentrations were found at agricultural and urban 

sites in the upper and lower Des Plaines River and the 

upper and lower Fox River. Downward trends in 

manganese concentrations were found at urban and 

agricultural sites scattered across the northern part of 

the upper Illinois River Basin. Trends in total recoverable strontium concentrations were downward at 

urban sites in the lower Des Plaines River and tributaries to the Calumet Sag Channel and were upward at 

agricultural sites on the main stems of the Kankakee, 

Iroquois, and Fox River Basins.

Smith and others (1987) reported that trends in 

iron and manganese were strongly related to trends in 

streamflow from 1974 through 1981. In the upper 

Illinois River Basin, streamflow at the time of sample 

collection trended downward from 1978 through 

1990 at only 6 of 38 sites: Sugar Creek at Milford 

(site 22), Des Plaines River at Russell (site 32), Illinois 

River at Marseilles (site 76), Fox River at Algonquin 

(site 89), Blackberry Creek near Yorkville (site 93), 

and the Fox River at Dayton (site 99). Sites where 

significant downward trends in streamflow were found 

were not the same sites where downward trends in 

barium, boron, iron, and manganese were found, 

except for the Illinois River at Marseilles (site 76). 

Thus, change in streamflow is not a likely explanation 

for the downward trends in these element concentrations from 1978 through 1990.

Most downward trends in dissolved lead 

concentrations in stream water across the conterminous United States from 1974 through 1981 have 

been attributed to the decrease in lead use (Smith and 

others, 1987). Gatz and others (1988) also reported a 

decrease in loading of atmospheric lead and cadmium 

over the Great Lakes during this period. Sites in or 

near the upper Illinois River Basin that were investigated by Smith and others (1987), however, generally 

did not show any trends in either dissolved or total 

recoverable lead concentration. Analysis of trends 

in dissolved and total recoverable lead in water in 

the upper Illinois River Basin was hindered by the 

large number of multiple minimum reporting levels. 

At only one site, the Des Plaines River at Lockport 

(site 42), were more than half of the observations of 

total recoverable lead above the minimum reporting 

level. Trend tests done with less-than values set to 

zero and to the minimum reporting level resulted in

different levels of significance, but neither set of tests 

indicated any change. One possible reason that no 

trends were observed for lead concentrations in water 

is that lead that has accumulated in the streambed 

sediment may be released to the water column, 

maintaining concentrations in water long after the 

initial source of the lead was removed.

Sediment

This description of major and trace elements in 

sediments is based on streambed-sediment data collected by the IEPA from 1978 through 1986, suspended-sediment data collected by the USGS at the eight 

NAWQA fixed sites from 1987 through 1990, and 

streambed-sediment data collected by the USGS 

during NAWQA synoptic samplings in 1987 and 1990.

Results of Streambed-Sediment 

Data Collection, 1978-87

EyJohn A. Colman

Historical concentrations of streambed sediments are based on sieved and unsieved sediments 

collected by IEPA from 1978 through 1987. 

Percentiles for concentrations from the sieved and 

unsieved data sets are summarized in table 11. As 

mentioned previously, only 10 elements were measured in nearly every sample: arsenic, cadmium, 

chromium, copper, iron, lead, manganese, mercury, 

phosphorus, and zinc (table 11). Exceptions were 

arsenic and manganese in the unsieved data set, 

which were measured at only 54 to 56 sites as compared to 80 to 103 sites for the other eight elements. 

If two or more samples were collected at a site, only 

the data from the most recent sampling were used for 

statistical analysis.

Three characteristics of IEPA site distribution 

are evident from the location map (fig. 6): (1) the 

coverages by method are not uniformly distributed, 

(2) large parts of the study area (Indiana, Wisconsin, 

and the Iroquois River in Illinois) were not sampled 

by either method, and (3) site distribution is biased 

toward the high-order streams. The nonuniform 

coverage precludes statistical analysis of the lumped 

data set because the differences between sieved and 

unsieved samples could not be distinguished from 

the effects of spatial or temporal differences. The 

spatial and stream-order bias of the data restrict the

38 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
applicability of interpretation to the sampled areas 

rather than to the whole basin.

Spatial patterns were examined using the 

Kruskal-Wallis one-way ANOVA test on concentrations in each subbasin. All the major streams of the 

upper Illinois River Basin were treated as separate 

subbasins except for those with insufficient coverage 

(the Iroquois River Basin, for instance). Coverages 

needed to be similar for an effective analysis, so 

subbasins with a large amount of data (for example, 

the Fox River Basin) were split. In addition, data 

from subbasins with too little data were combined, 

notably Salt Creek and North Branch Chicago River 

for sieved samples. The Tukey studentized range test 

was used to identify subbasins where differences in 

concentrations were significant; the results are given in 

tables 12 and 13.

For the sieved-sample data, only arsenic did not 

differ significantly among subbasins. Concentration 

ranks for most other elements were elevated in highorder streams as compared to ranks in low-order 

streams. Of these elements, cadmium was elevated in 

the East and West Branches of the Du Page River and 

in the Des Plaines River. Elements not significantly 

elevated in main stems as compared to tributaries were 

arsenic, manganese, and iron. Phosphorus concentrations were large throughout the Du Page River; it was 

also elevated in Salt Creek and North Branch Chicago 

River Subbasins. Generally, concentrations of 

elements in sieved samples from tributaries of the 

lower Fox River, of the upper Fox River, and of the 

Des Plaines River did not differ. Exceptions were 

found for chromium, iron, and lead, which were larger 

in tributaries of the Des Plaines River.

Sieved samples from subbasins in the Chicago 

metropolitan area contained larger concentration ranks 

of chromium, copper, mercury, and zinc (table 12). 

Subbasins that drain mainly urban areas include the 

Little Calumet River, lower Du Page River, East and 

West Branches of the Du Page River, Des Plaines 

River, Salt Creek, and North Branch Chicago River. 

Larger concentration ranks of arsenic, iron, and 

manganese, however, do not appear to be related to 

urban sources because relatively large concentrations 

were present in both agricultural and urban subbasins.

For the unsieved-sample data, ANOVA 

indicated that all elements were significantly different 

in at least one subbasin (table 13). In no case, 

however, was there a difference between tributaries to 

the Fox River and tributaries to the Illinois River.

Although the sites in the subbasins were not always the 

same for sieved- and unsieved-sample data, concentrations in the high-order streams tended to be larger than 

concentrations in low-order streams for both data sets.

Spatial-distribution anomalies can be assessed 

by comparing concentration data with average or 

background concentrations for a particular geology 

(Rose and others, 1979). No compendium of average 

or background concentrations for trace elements in 

stream sediments in the United States is available for 

samples that have been collected and analyzed in the 

same manner as these data. However, consistent 

information is available for background concentrations 

in streambed sediments in Illinois (Kelly and Kite, 

1984), as well as data collected nationwide for soil 

concentrations (Shacklette and Boerngen, 1984) 

(table 14). Data for streambed sediments at background sites in Illinois are available for unsieved 

sediments only, so that only unsieved-sample data can 

be compared directly with the background concentrations. Soil samples were collected at approximately 8-in. depth and at 50-mi intervals. Chemical 

analysis was done after complete digestion of the soil 

samples, in contrast to the analysis of streambed 

sediments by partial digestion.

The geometric means of the background concentrations in streambed sediments (Kelly and Kite, 

1984) were slightly smaller than means for concentrations in the soil samples (Shacklette and Boerngen, 

1984) (table 14), as would be expected considering the 

selection criterion for the background sites. Exceptions were iron, manganese, and phosphorus, which 

were substantially enriched in the streambed sediments 

from background streams. Sediment geochemistry 

likely contributed to the larger concentrations of these 

elements in background streams. Many concentrations of elements in streambed sediments in the upper 

Illinois River Basin (table 14) were elevated relative to 

background concentrations. Greater than 75 percent 

of the unsieved streambed-sediment samples were 

above the 98-percent confidence level for background 

concentrations of cadmium and lead. More than 

50 percent of the unsieved streambed-sediment 

samples were above the 98-percent confidence level 

for background concentrations of chromium, copper, 

mercury, and zinc, whereas 25 percent were above the 

98-percent confidence level for background concentrations of phosphorus. Arsenic, iron, and manganese 

seem to have been similar to background distributions.

Sediment 39
Large concentration ranks of chromium, copper, 

mercury, and zinc from unsieved sediments also were 

found in urban subbasins (Calumet Sag Channel, Little 

Calumet River, and North Shore Channel); however, 

the correlation is not as clear. This may be caused by 

coarse-grained sediments diluting the patterns 

indicated in the concentration ranks of fine-grained 

sieved sediments.

Correlations were found between some 

elements in the basinwide data sets for sieved and for 

unsieved samples (tables 15 and 16, respectively). 

These correlations are indicated by large (near 1.0) 

correlation coefficients. The correlation coefficients 

were calculated from log-transformed data. For 

sieved-sample data, the largest correlations (p > 0.90) 

were found among chromium, copper, and zinc. 

Correlations between this group and arsenic, iron, and 

manganese were low (p < 0.43). Correlations among 

the unsieved-sample data were not as large as for the 

sieved-sample data; coefficients for chromium, copper, 

and zinc in the unsieved-sample data ranged from 

0.80 to 0.85.

A useful method for grouping the correlations 

between elements is factor analysis. Factor analysis 

was applied to the log-transformed data. Sieved- and 

unsieved-sample data sets yielded two significant 

factors each (table 17). For sieved-sample data, the 

two-factor model accounted for 65 percent of the 

variance in the log-transformed data. The factor 

analysis results for sieved-sample data show that 

cadmium, chromium, copper, lead, mercury, phosphorus, and zinc are strongly associated (factor 1). 

The first factor accounts for approximately 54 percent 

of the variance of these elements. Manganese and 

arsenic also are strongly associated with the sievedsample data set (factor 2).

The factor analysis for the data set of unsieved 

samples did not include arsenic, cadmium, iron, and 

manganese because of missing values in the data set 

for these elements. The two-factor model for the 

remaining six-element data set accounted for 90 percent of the total variance. The larger percentage of 

variance explained as compared to the unsievedsample data is expected because of the reduced 

number of elements. Chromium, copper, lead, 

mercury, and zinc were associated in the unsievedsample data set (factor loading greater than 77 percent). The second factor carries a large loading for 

phosphorus.

As discussed previously, unsieved sediments at 

a large percentage of upper Illinois River Basin sites 

were enriched in all elements except arsenic, iron, and 

manganese. Although the sources that may be 

contributing to enrichment are too numerous to be 

individually assessed in this report, some generalizations can be made. Current mining activity, other 

than rock and gravel quarrying, is not present in the 

upper Illinois River Basin. Point sources of trace 

metals in the Chicago metropolitan area contain 

combined concentrations from wastewater-treatmentplant outfalls and storm-sewer overflows because 

many industries in the area discharge to sewagetreatment plants. Thus, the point-source effects of 

mine tailings, chlor-alkali plants, paper mills, and so 

forth, which are responsible for the largest anthropogenic metal enrichments of sediments worldwide 

(Forstner and Wittman, 1979), cannot be distinguished 

individually in the upper Illinois River Basin. The 

large industrial base in the basin does contribute trace 

metals. This contribution, however, may be input 

more from diffuse sources such as atmospheric 

deposition or combined sources from municipal 

wastewater-treatment plants and sewer overflows.

The "averaged" input from municipal and 

nonpoint sources may serve to explain the results of 

the factor analysis. The factors are results of both 

anthropogenic mobilization of elements in the basin 

as well as geochemical occurrence and deposition 

processes; that is, geochemical processes serve to 

concentrate insoluble elements in the sediments, but 

sources of elements are also necessary for elevated 

sediment concentrations to be observed. The implication of the large loading of several elements on one 

factor is that either the sources of the various elements 

are related or that a single large nonpoint source, such 

as atmospheric deposition or urban runoff, contributes 

many elements over a wide area.

Results of Suspended- and Streambed-Sediment 

Data Collection, 1987-90

Observation of spatial distributions of the trace 

elements in stream sediment was possible because 

most observations were above the minimum reporting 

level, in contrast to the many trace element concentrations in water that were below the minimum reporting 

level. In addition, stream-sediment samples are less 

likely to be contaminated during sampling and analysis 

than water samples because concentrations usually 

are much larger in stream sediments (table 18). For

40 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
example, total recoverable chromium concentrations in 

water in the upper Illinois River Basin were commonly 

in the range of less than 5 to 420 Jlg/L, whereas 

concentrations of chromium in suspended sediment 

ranged from about 16 to 980 Jlg/g and in streambed 

sediment ranged from 17 to 640 jig/g (table 18). Out 

of all the suspended-sediment data collected as part of 

the NAWQA program at the eight fixed sites, only 

concentrations of beryllium were consistently below 

the minimum reporting level. Almost all other 

elements in suspended sediment were found at concentrations above the minimum reporting levels (fig. A3). 

Concentrations of cadmium, molybdenum, and silver 

were below the minimum reporting level in streambed 

sediments from sites outside of the Chicago area 

(Colman and Sanzolone, 1991).

For most elements, suspended-sediment data 

from the eight NAWQA fixed sites did not provide an 

adequate representation of the range of concentrations 

observed in streambed sediments in the upper Illinois 

River Basin (table 18). Concentrations of only 

beryllium, cadmium, and silver in suspended 

sediments collected during 1987 through 1990 are 

within a similar range for concentrations in streambed 

sediments collected during the 1987 NAWQA 

synoptic sampling.

Most of the priority pollutants were found 

in larger concentrations in streambed sediments from 

urban sites. Streambed sediments from the urban 

sites typically had concentrations that can be considered elevated compared to the range found in background concentrations in nonindustrial, low-order 

streams in the Illinois River Basin (Mathis and 

Cummings, 1970) (table 1). Largest concentrations 

of antimony, boron, cadmium, chromium, copper, 

lead, mercury, nickel, silver, and zinc were found 

in suspended and streambed sediments from the 

Chicago area. The signature of this suite of 

elements continued downstream in Illinois River 

sediments, although concentrations were diluted by 

sediment originating from the Fox and Kankakee 

River Basins (Colman and Sanzolone, 1992). 

Cadmium concentrations in fine-grained streambed 

sediments in the North Branch Chicago River, 

Calumet Sag Channel, Chicago Sanitary and Ship 

Canal, lower Des Plaines River, and the Illinois River 

exceeded 4 jig/g and in some cases were as large as 

46 Jlg/g (Colman and Sanzolone, 1991). This range 

in concentration is two orders of magnitude larger than 

that reported for unsieved sediment from nonindustrial

streams (Mathis and Cummings, 1970) (table 1). 

Some of the largest concentrations of copper, lead, and 

zinc found in the upper Illinois River Basin are similar 

to concentrations of these elements in fine-grained 

sediments in Lake Ellyn, a small lake in a Chicago 

suburb (Striegl and Cowan, 1987). Large lead and 

zinc concentrations in Lake Ellyn were linked to urban 

runoff because road dirt also contained large concentrations of lead and zinc (Striegl and Cowan, 1987). 

Antimony and silver in sediments were associated 

with urban sources; however, in water, no spatial 

patterns could be distinguished because of the large 

number of observations below the minimum 

reporting level.

County wide aggregates of discharges of 

17 elements discussed in an IEPA report on toxic 

chemicals (Illinois Environmental Protection Agency, 

1991) (table 3) were compared to mean streambedsediment concentrations for high- and low-order 

streams in each county. Industries in Cook County 

release the largest amounts of aluminum, antimony, 

arsenic, cadmium, chromium, copper, lead, manganese, molybdenum, silver, and zinc compared to other 

counties in the Illinois part of the upper Illinois River 

Basin. The largest amounts of cobalt and nickel are 

released in Will County (Illinois Environmental 

Protection Agency, 1991). The largest concentrations of many of these urban-associated elements in 

sediments were observed in the industrial areas of 

Cook, Will, and Du Page Counties. Large concentrations of aluminum, barium, beryllium, cobalt, molybdenum, and vanadium in streambed sediments, however, were scattered across the upper Illinois River 

Basin at some agricultural and some urban sites. All 

were within the range found for background concentrations in rocks, soils, surficial deposits, and streambed 

sediments (table 1).

Although larger concentrations of many 

elements can be attributed specifically to urban or 

agricultural inputs, larger concentrations of some 

elements cannot be attributed to one source. Larger 

concentrations of arsenic in the Kankakee River suspended and streambed sediments, for example, are not 

directly related to inputs from agricultural practices, 

because large concentrations were not found in the 

Iroquois River Basin, which is more intensely farmed. 

Arsenic in streambed sediment was commonly found 

in concentrations from 20 to 140 Jlg/g in the Kankakee 

River (Colman and Sanzolone, 1991). Concentrations in suspended sediment from the Kankakee

Sediment 41
River at Momence (site 14) ranged from about 20 to 

50 fig/g (fig. A3). These concentrations are larger 

than background concentrations, which are typically 

less than 15 Jig/g. Only 1 to 4 percent of streambed 

sediments were clay sized in the Kankakee River 

(Gross and Berg, 1981), and sediments from the 

Kankakee River also contain larger iron and 

manganese concentrations than other streams in the 

upper Illinois River Basin. This pattern indicates that 

the small amount of fine-fraction sediments in the 

Kankakee River probably contain a greater proportion 

of iron and manganese coatings than is typical of other 

streams in the basin. Arsenic has been shown to have 

a large affinity for iron and manganese coatings 

(Horowitz, 1991). In addition, unsieved sediments 

from the Kankakee River were not enriched in arsenic, 

iron, or manganese, and neither were water samples 

collected during the NAWQA sampling.

Another possible source for arsenic in the 

Kankakee River Basin is shallow ground water. 

Shallow ground water in the Kankakee River Basin 

typically contains large arsenic concentrations (John 

Winters, Indiana Department of Environmental 

Management, oral commun., 1992) and is commonly 

used for irrigation in the basin. The coarse-grained 

soils in the Kankakee River Basin typically require 

more irrigation than the fine-grained soils in the 

Iroquois River Basin.

Concentrations of barium and strontium in 

water were larger from sites on the Fox River than 

other sites in the upper Illinois River Basin, and, in 

a previous section of the report, were attributed to 

ground-water contributions; however, only concentrations of strontium were larger in the Fox River stream 

sediments. Carbonate rocks contain considerably 

less barium than strontium (Hem, 1985), and strontium 

might possibly be leached from the carbonate particles 

in the Fox River and be transported in the water 

column. Barium, on the other hand, would be 

derived only from wastewater effluent originating 

from the Ordovician-Cambrian sandstone aquifer, 

where it is present in the dissolved phase (Gilkeson 

and others, 1983), and would not be associated with 

the carbonate-rich streambed sediments.

Other studies have identified element concentrations that are elevated or within normal background 

levels for example, Kelly and Kite (1984). As with 

the water data, methods of collection, preparation, and 

analysis may be different among studies. Sieving 

techniques are variable, with some investigators using

whole sediments and some sieving wet or dry 

sediments with different sized screens. Digestion 

techniques also can differ. Thus, any conclusions 

drawn from comparison of different data sets are 

limited by these factors. Background concentrations 

(those not related to human influences) also may cover 

a wide range, depending on the geologic setting in the 

study area (table 1).

Rickert and others (1977) proposed that probability plots of background concentrations in the Willamette River in Oregon, would follow a curve with 

few breaks. Breaks in curves of probability plots represent the delineation between background and elevated concentrations. Probability plots of chromium 

and lead (fig. 14) are similar to those found in Rickert 

and others (1977). Data for streambed sediment in 

these plots were divided into two groups, high-order 

streams and low-order streams. These plots show 

that high-order streams typically were more enriched 

with chromium and lead than low-order streams. The 

same relation between high- and low-order streams is 

found for the other priority pollutants that are not 

shown in figure 14. The curve for chromium at loworder stream sites does not appear to break, whereas 

the curve for high-order streams appears to break at 

about 90 fig/g. (In the Willamette River, the break in 

the chromium curve was at about 60 fig/g (Rickert and 

others, 1977).) Except for one data point, all the loworder stream data are below this concentration. This 

distribution of data indicates that background concentration for streams in the upper Illinois River Basin is 

less than 90 flg/g and that chromium is at background 

concentrations in the streambed sediment of most loworder streams.

Concentrations above 90 fig/g in streambed sediments 

were mainly clustered in the Chicago area (Colman 

and Sanzolone, 1992). Median concentrations above 

90 fig/g in suspended sediments were found at the 

Des Plaines River at Riverside (site 40), the Chicago 

Sanitary and Ship Canal at Romeoville (site 55), and 

the Illinois River at Marseilles (site 76). At the other 

five NAWQA fixed sites, few observations of chromium in suspended sediments were above 90 fig/g 

(fig. A3).

Probability plots for lead in streambed sediments in high- and low-order streams break at about 

40 fig/g (fig. 14), although the breaks are not as well 

defined as for probability plots of the chromium data. 

(In the Willamette River, the break in the lead curve

42 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
1,000

Q 

UJ 

COS

UJO

</>UJ 

Q.

So

100

§1

o

10

I I I I I I I I I

Median of 238 low-order sampling sites = 56.0 micrograms per gram

Median of 134 high-order sampling sites = 77.0 micrograms per gram A

A A

I I I I

+ LOW-ORDER STREAM SAMPLE 

A HIGH-ORDER STREAM SAMPLE

I____II II______I____

.01 .1 1 5 10 20 30 50 70 80 90 95 99 99.9 99.99 

PERCENT CHANCE OF EXCEEDING THE GIVEN CHROMIUM CONCENTRATION

10,000

OS 

UJ<

mcc 

SO

HI CC

ecu

1-0- <»</)

ZS-< 

zee 

oo

i i I i i i i i i r

- Median of 238 low-order sampling sites = 27.0 micrograms per gram

- Median of 134 high-order sampling sites = 75.0 micrograms per gram

1,000

100

isl 10

<Q 

UJUJ 

-1(0

A

+ LOW-ORDER STREAM SAMPLE 

A HIGH-ORDER STREAM SAMPLE

II II______|____

.01 .1 1 5 10 20 30 50 70 80 90 95 99 99.9 

PERCENT CHANCE OF EXCEEDING THE GIVEN LEAD CONCENTRATION

99.99

Figure 14. Probability distributions of chromium, lead, aluminum, and manganese in fine-grained streambed sediments in 

the upper Illinois River Basin.

Sediment 43
Q 

UJ

r»

II

oz 

o

u_f il

<Q

UJ

5

UJ

o

UJ

m

UJ

cc

H

z 

s

D 

Z

S

3

U_

O 

8

UJ

o

cc

UJ

10

0

Median of 238 low-order sampling sites = 5.2 percent 

Median of 134 high-order sampling sites = 5.3 percent

+ LOW-ORDER STREAM SAMPLE 

A HIGH-ORDER STREAM SAMPLE

II II______I

.01 .1 1 5 10 20 30 50 70 80 90 95 99 99.9 99.99 

PERCENT CHANCE OF EXCEEDING THE GIVEN PERCENTAGE OF ALUMINUM

10,000

1,000

100

Median of 238 low-order sampling sites = 685 micrograms per gram 

Median of 134 high-order sampling sites = 740 micrograms per gram

LOW-ORDER STREAM SAMPLE 

HIGH-ORDER STREAM SAMPLE

I II_____I_____

.01 .1 1 5 10 20 30 50 70 80 90 95 99 99.9 99.99 

PERCENT CHANCE OF EXCEEDING THE GIVEN MANGANESE CONCENTRATION

Figure 14. Continued. 

44 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
also was at about 40 |ig/g (Rickert and others, 1977), 

although the samples in that study were sieved to the 

less-than-20-|im fraction.) Concentrations of lead in 

streambed sediments above these breakpoints were 

also clustered in the Chicago area and near some 

medium-sized urban areas outside of Chicago (Colman 

and Sanzolone, 1992). In suspended sediments from 

the eight NAWQA fixed sites, median lead concentrations exceeded 40 |ig/g at all sites except the Iroquois 

River (site 28) (fig. A3).

In contrast, the curves from probability plots of 

aluminum and manganese show that concentrations in 

high-order streams were very similar to concentrations 

in low-order streams (fig. 14). The absence of a 

break in the curve for aluminum indicates that all 

concentrations of aluminum in streambed sediment in 

the upper Illinois River Basin were equal to or less 

than background concentrations. The curve for 

manganese seems to break slightly around 1,500 |ig/g. 

Concentrations above 1,500 |ig/g were found in 

streambed sediments from the high-order streams of 

the Kankakee River and occasionally from low-order 

streams scattered through the Chicago metropolitan 

area. Median concentration of manganese in suspended sediment from the Kankakee River was about 

4,500 ng/g (fig. A3). Median concentrations in 

suspended sediment from the Des Plaines and Illinois 

Rivers were between 1,500 and 2,000 |ig/g (fig. A3).

Breaks in the curves on the probability plots 

were compared to a classification scheme designed by 

Kelly and Kite (1984) that identifies levels of contamination of selected elements in Illinois stream 

sediments (table 19). Concentrations of elements 

cannot be compared directly because Kelly and Hite's 

scheme was based on unsieved sediments that were 

partially digested, in contrast to the NAWQA samples 

that were sieved and totally digested. Nevertheless, 

the breaks in the curves most commonly are near the 

"elevated" to "highly elevated" concentrations reported by Kelly and Hite (1984), except for chromium. 

Concentrations from the fine-grained sediment were 

expected to be larger than those concentrations 

identified as "slightly elevated" in table 19 because the 

elements are known to be more concentrated in the 

fine-grained sediments. The break in the probability 

curve for chromium (90 |ig/g) corresponded to a 

concentration greater than "extreme" in Kelly and 

Hite's (1984) classification. It is not known why the 

break in the probability curve for chromium is at a 

more extreme classification than the breaks for the

other elements. Chromium concentrations have been 

shown to have larger correlation coefficients with 

grain size than some of the other elements listed in 

table 19 (Horowitz, 1991); however, the correlation 

coefficients probably are not appreciably different to 

explain such a large difference in classification.

Probability plots are helpful in establishing 

general guidelines for distinguishing background from 

elevated concentrations of elements in streambed 

sediments. Elevated concentrations defined in this 

manner have no significance in terms of ecosystem 

health or water-quality criteria; they simply are 

anomalously large compared to the rest of the samples. 

On the basis of probability plots, concentrations in 

fine-grained streambed sediments larger than the 

following concentrations can be considered elevated in 

the upper Illinois River Basin: arsenic, 10 |ig/g; 

cadmium, 2 |ig/g; chromium, 90 |ig/g; copper, 

80 |ig/g; lead, 40 |ig/g; nickel, 50 |ig/g; and zinc, 

200 |ig/g (table 19). These concentrations are similar 

but somewhat larger than those for Great Lakes harbor 

sediments classified "heavily polluted," and they fall 

between the "lowest effect level" and "severe effect 

level" of Ontario sediment-quality guidelines (table 5).

Correlations Among Major and Trace Elements in 

Sediment, 1987-90

Correlation coefficients were computed for 

ranked element data from suspended-sediment samples 

collected at the eight NAWQA fixed sites from 1987 

through 1990 (table 20) and for streambed-sediment 

samples collected in 1987 (Colman and Sanzolone, 

1991) (table 21). Correlation analysis also was done 

on other physical and geochemical characteristics that 

have been shown to control element concentrations in 

sediment. For suspended sediment, the characteristics included discharge, sediment surface area, proportion of the sample less than 0.062 mm, suspendedsediment concentration, and total organic carbon 

concentration. Total organic carbon data also were 

analyzed for streambed sediments collected in 1987.

Correlations among the priority pollutants were 

strong in sieved streambed sediments from high-order 

streams sampled by NAWQA in 1987 (Colman and 

Sanzolone, 1991); in a previous section of this report, 

correlations were shown to be strong among priority 

pollutants in sieved streambed sediments collected by 

IEPA from 1982 through 1987 (table 15).

Correlations among priority pollutants in suspended sediment were similar to correlations among

Sediment 45
priority pollutants in streambed sediments. These 

correlations by means of two examples, one for copper 

and zinc, and one for chromium and nickel are shown 

in figure 15. Correlation coefficients from suspended-sediment data were greater than 0.65 for all correlations among antimony, cadmium, chromium, copper, 

lead, nickel, silver, and zinc. Cahill and Steele 

(1986) observed similar correlations among priority 

pollutants in backwater sediments from the Illinois 

River.

Many studies have shown that concentrations 

of chromium, copper, lead, nickel, and zinc in streambed sediments are affected by or correlated with 

clay-mineral content, particle size, and the amounts 

of organic material, total extractable iron, iron 

hydroxides, total extractable manganese, and 

manganese hydroxides (Leed and Belanger, 1981; 

Forstner and Salomons, 1983; Alberts and others, 

1984; Johnson, 1986; Horowitz and Elrick, 1987; 

Holden, 1989; Horowitz and others, 1989). In studies 

in or near the upper Illinois River Basin, significant 

correlations were found between these metals and clay 

content and organic content in the upper Mississippi 

River sediments (Bailey and Rada, 1984; Buhl and 

McConville, 1984), upper Peoria Lake sediments 

(Collinson and Shimp, 1972), and backwater 

sediments along the Illinois River (Cahill and Steele, 

1986). In this study, concentrations of chromium, 

copper, lead, nickel and zinc in suspended sediment 

from the eight NAWQA fixed sites did not correlate 

with surface area, amount of sample less than 

0.062 mm, total organic carbon content, or iron 

and manganese concentrations. As an example, 

figure 16 illustrates the lack of correlations between 

copper concentrations and surface area and between 

nickel concentrations and surface area in suspended 

sediments. Considerable scatter in concentrations is 

evident in the range of 5 to 20 square meters per gram.

Correlations from individual NAWQA fixed 

sites (table 20) were examined to determine whether 

the lack of correlation observed between the urbanassociated metals and other elements and properties 

was related to the mixing of data from individual sites 

with varying correlations. The difference in correlations between surface area and copper and nickel 

differed from site to site is shown in figure 17. 

Although copper did not correlate with surface area at 

the Iroquois River (site 28), copper and surface area 

negatively correlated (p = -0.58) at the Illinois River 

(site 76) (fig. 17). Nickel in suspended sediment

from the Iroquois River (site 28) and the Illinois River 

(site 76) did not correlate with surface area (fig. 17); 

however, correlations were found for the Kankakee 

River (site 14) and the Fox River (site 99) (table 20).

Chromium, copper, lead, nickel, and zinc 

concentrations in suspended sediment did not correlate 

with streamflow in the upper Illinois River Basin in 

data from all eight NAWQA sites combined. However, lead and nickel in suspended sediments positively correlated with streamflow at the Fox River at 

Dayton (site 99) (p = 0.57 and 0.56, respectively), 

whereas lead and nickel negatively correlated with 

streamflow at the Illinois River at Marseilles (site 76) 

(p = -0.62 and -0.64, respectively). These substantial differences indicate that the correlation between 

metal concentrations and streamflow is complex and 

not predictable from site to site in the upper Illinois 

River Basin.

Two priority pollutants, arsenic and beryllium, 

did not correlate with the other priority pollutants in 

suspended sediment or in streambed sediment. As 

mentioned earlier, large concentrations of arsenic and 

beryllium in streambed sediments were not limited 

to urban areas. In suspended sediments, beryllium 

strongly correlated with aluminum, iron, potassium, 

vanadium, and surface area, and inversely correlated 

with calcium. Thus, beryllium concentrations in 

suspended sediment seem to be strongly related to clay 

minerals. Arsenic in suspended sediment from the 

eight NAWQA fixed sites combined, correlated with 

iron (p = 0.67) but did not correlate with the other 

clay-mineral-related elements. Correlations from the 

individual sites show that arsenic correlated with iron 

at only four of the NAWQA fixed sites (table 20).

Correlations between arsenic and iron and 

manganese concentrations in suspended sediments 

were generally similar (but weak) in magnitude. This 

result contrasts with the Forstner and Salomons (1983) 

finding that arsenic is commonly associated more with 

iron coatings than with manganese coatings or organic 

material. At the Kankakee River at Momence 

(site 14), for example, correlation coefficients were 

large between arsenic and iron and arsenic and manganese (p = 0.80 and 0.79, respectively). At the 

Iroquois River near Chebanse (site 28), in contrast, 

arsenic correlated weakly with iron (p = 0.32) and did 

not correlate with manganese. At the Chicago 

Sanitary and Ship Canal (site 55), neither iron nor 

manganese correlated with arsenic. Arsenic in 

streambed sediment correlated weakly with iron

46 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
1-

z

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900

800

700

600

500

400

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1,600

1,400

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1,000

800

600

400

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_,,,, i ,,,,,,,,, Q , ,,,,,,,,,,,,,,,,,,_

: o° P = 0.95 ;

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: ^^^^ :

~_ ^gi? ° ~

r^frW^ i , , , , i , , , , i , . , , i , , , , i , , , , :

50 100 150 200 250 300 3J

NICKEL IN SUSPENDED SEDIMENT,

IN MICROGRAMS PER GRAM

O

o

p = 0.86

1 ° '.

O °°

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H

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0 0 °Q)

~: °°%&r ' - 9& Q

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Qi , , 1 , , , 1 . , . 1 . . . 1 . . . 1 . . . 1 , , i 1 , i , 1 i . . 1 . . .

100 200 300 400 500 600 700 800 900 1,(X

COPPER IN SUSPENDED SEDIMENT, 

IN MICROGRAMS PER GRAM

Figure 15. Correlations among selected priority pollutants in suspended sediments from the 

upper Illinois River Basin (p = Spearman's ranked correlation coefficient).

Sediment 47
350

300

Q DC 250 

UJ(3

QliJ

\UtL 200

111^ 

CL< 

(/)DC 150

z£ £2 100

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800

600

400

200

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O 

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p = 0 (not significant)

50

0 10 20 30 40 50

SURFACE AREA, IN SQUARE METERS PER GRAM

Figure 16. Correlations between surface area and copper and nickel 

concentrations in suspended sediments from the upper Illinois River Basin 

(p = Spearman's ranked correlation coefficient).

48 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
SITE 28, IROQUOIS RIVER 

NEAR CHEBANSE, ILLINOIS

SITE 76, ILLINOIS RIVER 

AT MARSEILLES, ILLINOIS

/u

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(not significant) .

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SURFACE AREA, IN SQUARE METERS PER GRAM

40 50

Figure 17. Correlations between surface area and copper and nickel concentrations in suspended sediments at two sites 

in the upper Illinois River Basin (p = Spearman's ranked correlation coefficient). (Site numbers refer to table 6.)

Sediment 49
(p = 0.41). Correlations between arsenic and iron in 

historical streambed-sediment data (table 15) were 

even weaker (p = 0.30).

In suspended sediments (table 20) and in 

streambed sediments (table 21), correlations were 

strong among aluminum, potassium, and vanadium 

(p > 0.84). These three elements in suspended 

sediment also correlated with sediment surface area 

and inversely correlated with calcium concentrations. 

Correlations with surface area seem to form a logarithmic curve (fig. 18). Cahill and Steele (1986) 

found that aluminum, potassium, and vanadium in 

streambed sediments are related to clay minerals in 

the clay-sized fraction of the sample. The inverse 

correlation of aluminum, potassium, vanadium, and 

surface area to calcium in the sediment in the upper 

Illinois River Basin indicates that calcium may be 

derived from larger grained particles of calcite. 

Calcite typically has a smaller surface area than most 

clay minerals (Horowitz, 1991). Therefore, smaller 

surface areas may indicate a greater amount of calcite 

in the suspended sediments, whereas larger surface 

areas may indicate a greater amount of clay minerals in 

the sediment. Most suspended sediments sampled 

contained a larger proportion of clay- and silt-sized 

particles (greater than 80 percent) (Sullivan and 

Blanchard, 1994).

Iron correlated with aluminum at all but 

one NAWQA fixed site and also with vanadium 

(p = 0.70) and surface area (p = 0.72). The relation 

between iron and aluminum in suspended sediment 

from an agricultural and urban site is shown in 

figure 19. Horowitz (1991) reported that, in general, 

iron is not considered a common component of clay 

minerals; instead, it is associated with iron oxide 

coatings on the surfaces of particulates. It is possible 

that the aluminum- and vanadium-containing clay 

minerals provide a large surface area that can be 

coated with iron oxides.

Seasonal Variations and Long-Term Changes, 

1978-90

Seasonal variations in median element concentrations in suspended sediment were significant at each 

of the eight NAWQA fixed sites (Kruskal-Wallis 

ANOVA, p < 0.10). Seasonal variations in median 

concentrations in suspended sediments, however, 

did not relate to seasonal variations in median total 

recoverable concentrations from the same eight sites, 

nor did they relate to discharge, volatile and total

suspended-solids concentrations, or suspendedsediment concentrations. Concentrations of many 

elements in suspended sediment, including aluminum, 

antimony, beryllium, cobalt, iron, manganese, nickel, 

and vanadium, were largest in February. However, 

monthly variations were not similar among any 

element concentrations for the rest of the months. 

As mentioned previously, pH was lowest in February; 

thus, pH may have been a factor in controlling the 

concentrations of elements associated with the suspended sediment. When pH is low, these elements seem 

to accumulate in larger concentrations in the suspended sediment than when pH is high.

No trend analyses were done on elements in 

suspended sediment or streambed sediment because 

the sampling periods were too short. In general, 

concentrations were similar between streambed 

sediments collected by USGS in 1987 and sieved 

streambed sediments collected by IEPA from 1982 

through 1987. Elements associated with urban 

sources from the IEPA data also were associated with 

urban sources in the 1987 USGS data. Two exceptions were chromium and manganese, which were 

larger in samples collected during the 1987 NAWQA 

synoptic sampling than identified in IEPA data collected from 1982 through 1987. Different analytical 

techniques (partial digestions for the IEPA data and 

total digestions for the NAWQA data) may account for 

these differences.

Biota

Results of Biotic Data Collection, 1989 and 1990

Major element and trace element concentrations 

in biota from the upper Illinois River Basin were interpreted on the basis of samples collected from 15 sites 

in 1989 and 25 sites in 1990 (table A1). Comparisons 

of element concentrations in biota among sites could 

not be statistically examined because of an insufficient 

number of samples at any one site and for any one 

species of biota. However, histograms of selected 

elements in fish livers, mollusks, caddisflies, crayfish, 

and plants (figs. 20-23, respectively) indicate the wide 

variability and possible enrichment of some elements 

in biota in the upper Illinois River Basin.

Comparable data from the literature were 

limited for evaluation of element concentrations in 

biota from the basin. Although some element 

concentrations in soft tissues of mollusks could be

50 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
UJ

2

Q 

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20

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p = 0.78 

O

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p = 0.81

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5 10 15 20 25 30 35 40 45

SURFACE AREA, IN SQUARE METERS PER GRAM

50

Figure 18. Effects of sediment surface areas on concentrations of aluminum and calcium in suspended 

sediments from the upper Illinois River Basin (p = Spearman's ranked correlation coefficient).

Biota 51
IROQUOIS RIVER NEAR CHEBANSE, ILL. (SITE 28)

H 

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CHICAGO SANITARY AND SHIP CANAL AT ROMEOVILLE, 

ILL. (SITE 55)

9

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IRON IN SUSPENDED SEDIMENT, IN PERCENT

Figure 19. Relations of aluminum and iron in suspended sediments 

at two sites in the upper Illinois River Basin, 1987-90 (p = Spearman's 

ranked correlation coefficient). (Site numbers refer to table 6.)

52 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
1.4 

1.3 

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SITE NUMBER 

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B 1990

MINIMUM REPORTING

= =

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38 40 53 58

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63 66 69

DU PAGE

76

ILLINOIS

80 81 

Figure 20. Element concentrations in common carp and white sucker livers from the upper Illinois River Basin, 1989-90. 

imum reporting level were set to 0.1 microgram per gram.) (Site numbers refer to table 6.)
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54 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
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53

 

H 

KANKAKEE
converted to wet weight (by use of the percent 

moisture values obtained for each composite sample) 

and compared to the Median International Standard 

(MIS) for marine shellfish (Nauen, 1983), element 

concentrations in fish livers from this study are not 

directly comparable to concentrations in whole fish 

collected by the National Contaminant Biomonitoring 

Program (NCBP) of the U.S. Fish and Wildlife Service 

(Schmitt and Brumbaugh, 1990). (As of 1991, the 

NCBP is now known as the Biomonitoring of Environmental Status and Trends (BEST) program.) With 

the exception of aluminum and mercury, concentrations of elements in whole fish are generally lower 

than in fish livers (Bollingberg and Johansen, 1979; 

Boyer, 1984; Saltes and Bailey, 1984; Brumbaugh and 

Kane, 1985; Cuvin-Aralar and Furness, 1990; Harrison 

and Klaverkamp, 1990). Wiener and others (1984) 

found significant correlations between whole common 

carp and common carp liver for concentrations of 

cadmium, mercury, and lead in the upper Mississippi 

River; sites where large concentrations were found in 

whole fish also were sites where large concentrations 

were found in livers. Unfortunately, no NCBP/BEST 

sites are located in the upper Illinois River Basin so 

that such a comparison could be made for the basin. 

Concentrations of some elements in fish livers were 

converted to wet weight (by use of the percent 

moisture values obtained for each composite sample) 

and compared to the EDL 85 and 95 for livers of freshwater fish in California's TSMP (Rasmussen, 1992). 

The EDL 85 and 95 values were based on TSMP data 

for fish collected from various inland waters in 

California from 1978 through 1990. These values 

were generated to allow determination of elevated 

contaminant levels in California and do not represent 

national guidelines or toxic-effect levels. At present, 

neither national guidelines nor sufficient comparable 

data from the literature are available to determine the 

toxic effects of element concentrations in biota from 

the upper Illinois River Basin.

The variety of species collected at sites in 1989 

and 1990 also made comparisons for element concentrations in biota among subbasins difficult. Even 

comparisons for the largest data set, common carp, 

were limited with only one or less representative site in 

three of the six subbasins within each year (fig. 20). 

Still, tentative conclusions may be possible. For 

example, arsenic concentrations in common carp livers 

were generally larger from the Kankakee and Fox 

River Basins than from the other basins (fig. 20),

manganese concentrations were generally larger in the 

Kankakee River Basin, and vanadium concentrations 

were generally larger in the Fox River Basin than in 

the other basins (table Al).

Concentrations of the major elements 

aluminum, boron, iron, and manganese were 

variable among biota. With the exception of 

iron, concentrations of these elements were smallest 

in fish livers. Concentrations of aluminum were 

near or below the minimum reporting level in most 

samples of fish livers; exceptions included a concentration of 13.0 (ig/g in common carp livers from the 

Kankakee River at Momence (site 14) in 1989 and a 

concentration of 54 (ig/g aluminum in common carp 

livers from the Fox River at Dayton (site 99) in 1990 

(table A1). Boron concentrations in sago pondweed 

(Potamogeton pectinatus) (fig. 23b) and crayfish 

(fig. 22b) from two sites on the Little Calumet River 

(sites 53 and 52, respectively) indicate enrichment in 

this urban/industrial stream. Crayfish from the Little 

Calumet River (site 52) contained 120 ^lg/g boron; this 

concentration was at least 20 times those found in 

crayfish from other sites in the basin (fig. 22b). 

Although no water or sediment data are available for 

this site in 1989, large total recoverable and dissolved 

boron concentrations were found during the summer of 

1990. The largest concentrations of aluminum and 

iron in biota (2,140 p,g/g and 2,370 p,g/g) were 

observed in caddisflies from Salt Creek (site 38) in 

1989 (table Al). Concentrations of manganese in 

crayfish collected in 1989 from Indian Creek (site 97) 

and the North Branch Chicago River (site 45) were 

approximately five times those in crayfish at the 

Des Plaines River (site 40) (table Al), possibly 

indicating manganese enrichment at these two sites.

Concentrations of lead, molybdenum, and silver 

were below minimum reporting levels in most samples 

of biota, and beryllium was below the minimum 

reporting level in all samples (table Al). Although 

concentrations of boron, chromium, nickel, and lead 

were measurable in most samples of aquatic plants 

(fig. 23), concentrations of these elements were below 

minimum reporting levels in fish livers at all sites 

(table A1). The scarcity or absence of those elements 

at detectable concentrations in the sampled organisms 

indicates that concentrations of these elements were 

generally small in biota from the basin; however, it 

may mean either that some tissues were insensitive 

measures of contamination of these elements or that 

more sensitive methods of analysis need to be used,

68 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
especially for lead (minimum reporting level between 

4 and 6 (ig/g). For example, the largest lead concentration in streambed sediment sampled in 1990 was 

260 |ig/g from the Des Plaines River above Brandon 

Road Dam at Joliet (site 58) (table A3). Colman and 

Sanzolone (1991) reported a concentration of 440 jig/g 

in a sample of streambed sediments collected from this 

site in 1987, and this concentration ranked eighth out 

of 135 high-order sites. Only fish livers, however, 

were sampled at this site, and lead concentrations in 

these tissues were below the minimum reporting level 

of 4 ^ig/g. Use of good indicator organisms or tissues 

and sensitive analytical methods capable of achieving 

environmentally relevant minimum reporting levels is 

critical for interpretation of small concentrations of 

trace elements.

Several trace elements seem to be enriched in 

biota from sites in the upper Illinois River Basin when 

compared to other sampled sites or literature values. 

Unlike water and sediment data, however, spatial 

patterns of some urban- or soil-associated elements 

were not readily apparent in the biotic data; thus, 

concentrations of these elements are discussed 

separately for each element.

Arsenic concentrations in biota from the basin 

were largest at sites in areas of agricultural land use. 

Most arsenic concentrations in fish livers from the 

basin were near or below the minimum reporting level 

except for a composite sample of common carp livers 

from the Kankakee River at Momence (site 14) in 

1989 (fig. 20a). The concentration of 1.3 ^ig/g in 

livers from this agricultural site exceeded the TSMP 

EDL 85. This concentration was also larger than that 

found for livers of common carp by Wiener and others 

(1984) for the upper Mississippi in 1979. The arsenic 

concentration in Asiatic clams (Corbicula flumined) 

(fig. 2la) from the Kankakee River at Momence 

(site 14) was also relatively large compared to concentrations in this species from the Du Page River at 

Shorewood (site 69), an urban site. The largest 

arsenic concentrations in biota were found in elktoe 

clams (Alasmidonta marginatd) from Honey Creek 

(site 80), another agricultural site and a Fox River 

tributary, in 1990. The two highest arsenic concentrations in crayfish were found at the only two agricultural sites sampled for crayfish (fig. 22a). Concentrations of 2.1 and 2.9 |ig/g were found in crayfish 

from Honey Creek (site 81) and Indian Creek (site 97), 

respectively, both are agricultural sites and Fox River 

tributaries. Indian Creek (site 97) had been selected

as a reference site for the Central Corn Belt Plains 

(CCBP) ecoregion. At six other sites that represented 

urban land uses in the CCBP ecoregion, arsenic 

concentrations in crayfish were 1.4 ^ig/g or less. 

These results indicate that biota from three agricultural 

sites, Kankakee River (site 14), Honey Creek (site 81), 

and Indian Creek (site 97) are enriched in arsenic.

Barium concentrations in biota from the upper 

Illinois River Basin indicate enrichment at urban as 

well as agricultural sites (table Al). In 1989, the 

largest barium concentrations observed in biota were 

89.6 and 129 ^ig/g in crayfish from Honey Creek 

(site 81), an agricultural site, and Indian Creek 

(site 97), a reference site, respectively. These values 

were more than twice those found in crayfish from 

other sample sites. The largest concentrations of 

barium in aquatic plants were found in sago pondweed 

from two urban/industrial sites, 38.9 and 47.3 |ig/g 

from the Little Calumet River at Calumet Park (site 

53) and the North Branch Chicago River at Niles (site 

45), respectively. Tazik (1988) reported 29.2 \Lg/g 

barium in shoots of this species collected from the Des 

Plaines River below Brandon Road Dam in 

1987. This indicates that concentrations of barium in 

biota are elevated at Honey Creek (site 81) and the 

North Branch Chicago River (site 45).

Cadmium concentrations in biota, although 

variable among sites and biota collected, indicate 

enrichment at six sites representing agricultural and 

urban land uses, as well as at one reference site. 

Cadmium concentrations in mollusks were less than 

1.0 n,g/g at 7 of 10 sites (fig. 2la), and concentrations 

at all sample sites were smaller than those reported for 

fat mucket (Lampsilis siliquoided) and five other 

species of clams collected from the Fox River in 

Illinois and Wisconsin in 1973 (Anderson, 1977). 

Eurasian water milfoil (Myriophyllum spicatwri) from 

the North Shore Channel (site 46) contained 8.6 ^ig/g 

cadmium (fig. 23a), and the cadmium concentration in 

whole snails from this site was 5.9 |ig/g (table Al). 

This concentration in milfoil is similar to that reported 

for milfoil species from a contaminated lake in Canada 

(Franzin and McFarlane, 1980), and it is much larger 

than that reported for milfoil species from the 

Des Plaines River in 1987 (Tazik, 1988) and the 

upper Mississippi River in 1977 (Buhl and McConville, 1984). Although concentrations were near or 

below the minimum reporting levels in crayfish and 

in white sucker (Catostomus commersoni) livers 

(table Al), concentrations in common carp livers from

Biota 69
12 sites exceeded the TSMP EDL 85. Concentrations 

of cadmium in carp livers from Iroquois River 

(site 28), Fox River (site 99), Big Rock Creek 

(site 94), Illinois River (site 76), and Des Plaines 

River (site 40) were elevated with respect to concentrations at other sites in the basin (fig. 20b), and these 

concentrations exceeded the TSMP EDL 95. These 

sites represent both agricultural and urban land uses. 

The concentrations of cadmium in carp livers of 

44.8 jig/g at the Iroquois River near Chebanse 

(site 28), 18.0 fig/g at the Fox River at Dayton 

(site 99), and 9.5 fig/g at the Illinois River at 

Marseilles (site 76) greatly exceeded concentrations 

reported by Wiener and others (1984) for carp livers 

collected from the upper Mississippi River in 1977; 

however, cadmium concentrations in streambed 

sediments were near minimum reporting levels in 1989 

and 1990 at Iroquois River near Chebanse (site 28) and 

Fox River at Dayton (site 99) (table A3). Most 

concentrations in carp livers from the upper Illinois 

River Basin were larger than those reported by Wiener 

and others (1984) for livers of common carp from the 

upper Mississippi River.

Chromium concentrations were found at larger 

concentrations in aquatic plants (fig. 23) than in other 

biota sampled in the basin, and concentrations in clams 

(fig. 2la), crayfish (fig. 22a), and fish livers (table Al) 

were near or less than the minimum reporting level of 

1 fig/g at all sites. Concentrations in plants ranged 

from 1 jig/g in curly leaf pondweed (Potamogeton 

crispus) at the reference site Mill Creek (site 2) to 

10 jig/g in sago pondweed from the Little Calumet 

River (site 53) and 11 fig/g in Eurasian water milfoil 

from the North Shore Channel (site 46). The concentration in sago pondweed is similar not only to the 

largest concentration reported by Tazik (1988) for 

shoots of this species from the Des Plaines River in 

1987 but also to means reported for shoots of broadleaf 

pondweed (Potamogeton americanus) from the upper 

Mississippi River in 1977 (Buhl and McConville, 

1984). Chromium in Eurasian water milfoil from 

the North Shore Channel (site 46) exceeds the range of 

2.3 to 8.9 fig/g reported by Tazik (1988) for shoots of 

milfoil species. These results indicate that aquatic 

plants at these two urban/industrial sites, the Little 

Calumet River (site 53) and North Shore Channel 

(site 46), are enriched in chromium.

Copper concentrations differed greatly among 

biota sampled in the basin, and tissue samples from 

many of the urban and agricultural sites seem to

contain elevated concentrations. The highest concentration of copper in soft tissues of clams was at the 

Du Page River at Shore wood (site 69) (fig. 21b). 

Samples of Asiatic clams from this site contained 

32.9 fig/g copper in 1989 and 38.6 fig/g in 1990. 

These concentrations were in the range of 23 to 

45 jig/g copper reported by Leland and Scudder 

(1990) for composite samples of Asiatic clams from 

the San Joaquin River in California but were higher 

than concentrations reported by Anderson (1977) 

for six other species of clams from the Fox River in 

1973. The largest copper concentrations in crayfish 

and aquatic plants were found at the North Branch 

Chicago River at Niles (site 45) in 1989 (figs. 22b 

and 23a). Replicate samples of crayfish from the 

East Branch Du Page River at Naperville (site 66) also 

contained large amounts of copper when compared to 

other sites in the basin (fig. 22b). Whole snails from 

the North Shore Channel (site 46) contained the largest 

copper concentration observed in all biota, 209 fig/g, 

and may indicate enrichment at this site. Most 

concentrations of copper in common carp livers 

(fig. 20c) and white sucker livers (fig. 20d) exceeded 

the TSMP EDL 85, and concentrations at six sites 

exceeded the TSMP EDL 95. Copper concentrations 

in carp livers were elevated at 15 of 17 sites with 

respect to concentrations at the Little Calumet River at 

Calumet Park (site 53) and the Des Plaines River 

above Brandon Road Dam at Joliet (site 58) (fig. 20c). 

The largest concentration was observed at Big Rock 

Creek (site 94), a Fox River tributary and a reference 

site for the CCBP ecoregion. When compared to 

samples from two Kankakee River tributaries, copper 

concentrations in white suckers were elevated at Mill 

Creek (site 2), the Mukwonago River (site 78), the 

East Branch Du Page River (site 66), and Blackberry 

Creek (site 93) (fig. 20d). As was observed for 

common carp, these sites include not only reference 

streams but also streams draining urban and agricultural land.

Lead concentrations in most biota were below 

the minimum reporting levels of 4 to 6 fig/g; however, 

a concentration of 9.0 fig/g lead was found in whole 

snails (table Al) and Eurasian water milfoil (fig. 23a) 

from the North Shore Channel (site 46). The largest 

lead concentration in aquatic plants from the basin 

(22 jig/g) was found in sago pondweed from the 

Little Calumet River (site 53). This lead concentration is similar to that reported by Franzin and 

McFarlane (1980) for plants of the same genus

70 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
from a contaminated lake in Canada. Lead concentrations in all species of pondweed (including sago 

pondweed) were below a minimum reporting level of 

1.2 |lg/g in Tazik's study (1988). Concentrations of 

lead in caddisflies (9.0 |ig/g) (table Al) and wild 

celery (Vallisneria sp.) (fig. 23a) (7.0 |lg/g) from Salt 

Creek (site 38) indicate that these biota are also 

enriched relative to biota from other sites in the 

basin. These data seem to indicate lead enrichment at 

the North Shore Channel (site 46), Little Calumet 

River (site 53), and Salt Creek (site 38), all of which 

represent urban land uses.

Mercury was found at small concentrations in 

most biota from the basin with the exception of fish 

livers. A mercury concentration of 0.55 |lg/g in 

white sucker livers from the Mukwonago River 

(site 78) was large when compared to approximately 

background concentrations of 0.1 |ig/g in white sucker 

livers from Kankakee River tributaries (fig. 20f). 

Livers of common carp from the West Branch Du Page 

River (site 63) contained 0.41 |ig/g mercury, and Fox 

River tributaries as a group yielded carp livers 

containing relatively large mercury concentrations 

(fig. 20e). The Illinois Fish Contaminant Monitoring 

Program of the IEPA found generally small concentrations of mercury in fish from the upper Illinois River 

Basin during 1974-82 (Illinois Environmental 

Protection Agency, unpublished data, 1987b); 

however, samples of single largemouth bass fillets 

collected from the Fox River near the IllinoisWisconsin State line and near Wedron, 111., in 1974 

contained relatively large concentrations of mercury 

compared to samples from other sites. These concentrations, however, did not exceed established 

U.S. Food and Drug Administration (USFDA) action 

levels for edible portions of fish (U.S. Food and Drug 

Administration, 1984). In the upper Mississippi 

River study by Wiener and others (1984), mercury 

concentrations in common carp livers were less than 

0.4 |ig/g at 12 of 15 sites. Samples of carp livers 

from three other sites had concentrations as large as 

7.91 |ig/g mercury. Using U.S. Fish and Wildlife 

Service's NCBP data, Wiener and others (1984) 

concluded that the concentrations in carp livers from 

the upper Mississippi River were large compared to 

concentrations in carp from other streams in the 

Nation. Relative to other sites in the upper Illinois 

River Basin, mercury concentrations in livers of 

common carp and white sucker indicate enrichment in 

the West and East Branches of the Du Page River

(site 63 and 66), Iroquois River (site 28), and in three 

tributaries of the Fox River: the Mukwonago River 

(site 78), Blackberry Creek (site 93), and Big Rock 

Creek (site 94) (figs. 20e and f). These sites 

represent a mixture of urban/residential and agricultural land uses; Big Rock and Blackberry Creeks were 

both rated "highly valued aquatic resources" by the 

IEPA on the basis of a 1982 survey of fish and invertebrate communities together with water quality and 

habitat sampling (Illinois Environmental Protection 

Agency, 1987a).

Nickel concentrations in biota were largest in 

aquatic plants (fig. 23a), whereas concentrations in 

crayfish (fig. 22a) and fish (table Al) were near or 

below the minimum reporting level of 2 |ig/g. A 

concentration of 36 |ig/g nickel in waterweed from the 

North Branch Chicago River at Niles (site 45) was the 

largest observed in biota from the basin. The largest 

nickel concentration in mollusks was 28.0 |ig/g, 

observed in whole snails from the North Shore 

Channel (site 46) (table Al). This nickel concentration was the largest in all invertebrates sampled, and 

it was three times larger than the next smallest observation in other invertebrates. Comparison data for 

these species is not available; however, such large 

concentrations may indicate nickel enrichment at these 

two urban sites. Nickel concentrations in Asiatic 

clams from the Du Page River at Shorewood (site 69) 

increased from 2.0 to 5.0 |ig/g from 1989 to 1990. 

Both concentrations are larger than those reported by 

Leland and Scudder (1990) for Asiatic clams from the 

San Joaquin River in California and may indicate 

nickel enrichment in this urban stream.

Selenium concentrations in biota were similar in 

occurrence to mercury concentrations (generally small, 

except in fish livers). Concentrations in the upper 

Illinois River Basin (table Al) were below the TSMP 

EDL 95 for freshwater fish from primarily selenium 

contaminated waters in California; however, selenium 

concentrations greater than 6 |ig/g were found at 

eight sites sampled for carp in the upper Illinois River 

Basin and are elevated with respect to a mean selenium 

concentration of 3.6 |lg/g for carp livers from the upper 

Mississippi River in 1979 (Wiener and others, 1984). 

The eight sites where selenium concentrations were 

elevated were Kankakee River (site 14), Des Plaines 

River and above Brandon Road Dam (sites 40 and 58), 

West Branch Du Page River (site 63), East Branch 

Du Page River (site 66), Illinois River (site 76), Honey

Biota 71
Creek (site 80), and Big Rock Creek (site 94). These 

sites represent urban and agricultural land uses.

Strontium concentrations differed by two orders 

of magnitude among the different groups of biota. 

The three largest concentrations found for mollusks, 

crayfish, and plants were from Salt Creek (site 38) 

(figs. 21b, 22b, and 23b). Fingernail clams and 

crayfish from this urban/industrial site contained 

582 and 562 |j,g/g strontium, respectively, and a 

concentration of 94.7 (ig/g was found in wild celery. 

Livers of common carp from this site also contained a 

large amount of strontium compared to carp livers 

from other sites in the basin (fig. 20g). Therefore, 

data for a variety of biota from Salt Creek (site 38) 

indicate strontium enrichment in this urban stream.

Zinc concentrations seem to be elevated at most 

sites sampled for fish livers in the upper Illinois River 

Basin. All concentrations of zinc in common carp 

livers were larger than 200 (lg/g and greatly exceeded 

the TSMP EDL 95 (fig. 20h). The largest concentrations in carp were at Salt Creek at Western Springs 

(site 38), Fox River at Algonquin (site 89), Fox River 

at Dayton (site 99), and one of two composite samples 

from Big Rock Creek (site 94). White suckers were 

enriched in zinc at four of seven sites sampled and 

exceeded the TSMP EDL 95 at East Branch 

Du Page River (site 66) and Blackberry Creek 

(site 93) (fig. 20i). Although no fish livers were 

collected from the reference site Langan Creek (site 

27), zinc concentrations in fat mucket clams from this 

Iroquois River tributary were at least four times larger 

than concentrations in other invertebrates and were 

much larger than concentrations reported for this 

species by Anderson (1977) for the Fox River in 

1973 (fig. 21b and 22b). In addition, this concentration of zinc in fat mucket clams from Langan Creek 

(site 27) greatly exceeded the MIS for marine shellfish. These results indicate that zinc concentrations 

at the reference site, Langan Creek (site 27), are 

elevated also.

Biota from some urban sites in the basin were 

enriched with respect to several elements. Relative to 

other invertebrates sampled, large concentrations of 

cadmium (5.9 ^ig/g), chromium (6.0 M£/g), copper 

(209 M-g/g), nickel (28 jig/g), and lead (9 ^ig/g) were 

found in whole snails from the North Shore Channel 

(site 46) in 1989 (fig. 21 and table Al), and large concentrations of chromium (11 (J-g/g), copper (38.4 (ig/g), 

and lead (22 (lg/g) were also found in Eurasian water 

milfoil from this industrial stream (fig. 23a). Another

industrial stream, the North Branch Chicago River at 

Niles (site 45), seems to be enriched in copper and 

nickel in biota. Copper concentrations in water at 

this site have exceeded the USEPA chronic waterquality criterion. Relative to values in the literature, 

concentrations of chromium (10 (lg/g), lead (22 (lg/g), 

and vanadium (5.6 ^lg/g) were also large in sago 

pondweed from the Little Calumet River at Calumet 

Park (site 53), a highly industrial site. Biota from 

Salt Creek (site 38), a residential stream, contained 

large concentrations of lead, manganese, nickel, and 

strontium when compared to biota from other sampled 

sites. Total recoverable concentrations in water from 

this site have exceeded the USEPA chronic criterion 

for lead.

Variations were observed between the 1989 and 

1990 synoptic surveys for some element concentrations in biota. Although 12 sites were sampled both 

years, only 5 sites were sampled for the same species 

of biota in both years; this incomplete correspondence 

between the two surveys precluded statistical analysis 

of the data. However, some element concentrations 

among this data set are worth noting. Asiatic clams 

sampled from the Du Page River at Shorewood (site 

69) had fairly similar concentrations of most elements, 

with the exception of nickel, as described earlier. 

In 1989, the concentration of arsenic in carp livers 

from the Kankakee River at Momence (site 14) was 

1.3 (lg/g; however, the concentration in 1990 was only 

0.3 (lg/g. Concentrations of aluminum and copper in 

carp livers from the Kankakee River (site 14) and the 

Des Plaines River above Brandon Road Dam (site 58) 

were smaller in 1990 than in 1989; cadmium and 

selenium concentrations were larger in 1990. Similarly, aluminum and copper concentrations were 

smaller in 1990 at the Illinois River at Marseilles 

(site 76), and cadmium and selenium concentrations 

were larger in 1990 at the Du Page River at Shorewood 

(site 69). Additional sampling would be needed to 

establish trends, such as whether cadmium and 

selenium concentrations in carp livers are increasing at 

these three sites.

In most cases where several species were 

collected from a site at one time, large concentrations 

of elements observed in one taxon were observed in 

the other species as well. Some exceptions were 

found. For example, concentrations of barium, 

cadmium, and nickel differed greatly between two 

species of mollusks at Honey Creek (site 80) in 1990 

(fig. 21b). Elktoe clams contained 124 ^ig/g barium,

72 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
whereas three ridge mussels (Amblema plicatd) from 

this site contained only 72.2 jig/g barium. These two 

species of mollusks from Honey Creek (site 80) 

differed considerably in their accumulation of 

cadmium also. Elktoe clams collected from Honey 

Creek (site 80) in 1990 contained 7.0 jlg/g nickel, 

whereas concentrations in three ridge clams from this 

site were below the minimum reporting level. 

Although the largest concentrations of barium in 

aquatic plants were observed in sago pondweed from 

the North Branch Chicago River at Niles (site 45) 

(fig. 23b), composite samples of crayfish collected at 

the same time from this site were not enriched in 

barium (fig. 22b). Chromium concentrations in four 

species of biota from Salt Creek (site 38) during 1989 

ranged from less than the minimum reporting level of 

1.0 jig/g (fingernail clams) to 5.4 jig/g (caddisflies). 

These results demonstrate the potentially large differences in element concentrations among species 

collected from a site and emphasize the importance of 

collecting more than one species at a site whenever 

possible.

Correlations Among Major and Trace Elements in 

Biota, 1989 and 1990

Spearman's rank correlation coefficients were 

calculated for concentrations of elements in tissues of 

common carp, white sucker, and crayfish collected 

from the upper Illinois River Basin during 1989 and 

1990 (table 22). Relations among a number of 

elements in these tissues were not possible because at 

least half of the concentrations were below minimum 

reporting levels. Correlations for concentrations 

between boron, barium, beryllium, chromium, lead, 

molybdenum, nickel, and silver in common carp livers 

could not be examined for this reason. More 

elements in white sucker livers could not be examined 

by correlation, than in common carp livers. In 

addition, correlations could not be examined for 

mollusks or aquatic plants because of insufficient 

single-species data. Nevertheless, correlations were 

found among some element concentrations in fish and 

also in crayfish tissues. This finding indicates similar 

spatial patterns in bioaccumulation for these elements.

In common carp livers, positive correlations 

were found among concentrations of copper, mercury, 

and zinc (p > 0.53); concentrations of cadmium, 

copper, and selenium also positively correlated with 

each other. Strontium negatively correlated with 

selenium (p = -0.47 to -0.51).

Although correlations among element 

concentrations in white sucker livers could be 

computed for only copper, iron, mercury, manganese, selenium, and zinc, some similarities were 

found between common carp and white sucker for 

correlations among elements in liver tissue. As 

was found for common carp, concentrations of copper, 

mercury, and zinc in white sucker livers all positively 

correlated with each other (p > 0.83), and positive 

correlations were found between concentrations of 

copper and selenium (p = 0.66). This similarly 

indicates a common source and mode of accumulation 

for these elements in livers of common carp and white 

sucker.

More correlations were observed among 

elements in crayfish tissues than were observed 

for fish. Some similarities were found between 

the two groups of biota. As was seen for common 

carp, a moderate positive correlation was found 

between concentrations of aluminum and strontium 

(p = 0.74). This positive relation of aluminum and 

strontium in both organisms was puzzling because, 

although aluminum was generally in the particulate 

phase, strontium was mostly in the dissolved phase in 

water samples from the basin. Concentrations of 

aluminum, chromium, iron, and vanadium positively 

correlated with each other in analyses of whole crayfish (p = 0.63 to 0.90). Aluminum, chromium, 

and vanadium were mostly in the particulate phase 

in water samples from the basin in 1989. In contrast, 

aluminum negatively correlated with manganese 

(p = 0.74). Elevated manganese concentrations in 

some organisms can interfere with iron absorption in 

the gut (Donaldson, 1980), so a negative correlation 

between these two elements in tissues was not 

unexpected. Significant negative correlations were 

observed between strontium and arsenic concentrations (p = 0.87) and strontium and barium concentrations (p = 0.71) in crayfish. Barium was mostly in 

the dissolved phase in water, as was strontium, and the 

two were strongly correlated with each other in that 

component. A positive correlation was found for 

tissue concentrations of selenium with concentrations 

of barium (p = 0.65).

Similar modes of uptake and accumulation, 

as well as physiological interactions, may help explain 

some of the correlations found in element concentrations of biota. Copper and zinc concentrations were 

positively correlated in common carp (p = 0.54), white 

suckers (p = 0.99), and crayfish (p = 0.62). As

Biota 73
mentioned earlier, both of these elements are nutritionally required, and they are essential for the proper 

functioning of several enzymes. They are physiologically regulated in vertebrates, and much of the copper 

and zinc in these organisms is found in the liver 

(Sternlieb, 1988).

Correlations of Element Concentrations 

Among Water, Sediment, and Biota

Ranked element concentrations were correlated 

among water, sediment, and biota. First, dissolved 

and total recoverable concentrations in water were 

compared to element concentrations in suspended 

sediment collected at the eight NAWQA fixed sites 

from 1987 through 1990. Next, concentrations in 

water were compared to element concentrations in 

streambed sediment collected at the same site or the 

nearest site upstream. Finally, concentrations in biota 

were compared to dissolved and total recoverable 

element concentrations in water, element concentrations in suspended sediment, and element concentrations in streambed sediment.

Even though general spatial patterns among 

water and suspended sediment were similar for the 

urban-associated elements antimony, boron, cadmium, chromium, copper, lead, molybdenum, nickel, 

and phosphorus (Appendix A), correlation coefficients 

among these elements in water and sediment were 

generally negligible (table 23). Only antimony, cadmium, nickel, and phosphorus in suspended sediment 

correlated (p = 0.52 to 0.60) with either dissolved or 

total recoverable concentrations of the same element. 

The correlations are so few probably because of the 

large number of observations of dissolved and total 

recoverable concentrations below the minimum 

reporting level for many of the urban-associated 

elements.

Chromium, cobalt, and nickel concentrations in 

suspended sediment negatively correlated with both 

alkalinity and with pH in water (p = -0.57 to -0.76). 

Aluminum, arsenic, and beryllium in suspended 

sediment negatively correlated with alkalinity 

(p = 0.50 to 0.53), and antimony and molybdenum in suspended sediment negatively correlated 

with pH (p = 0.57). The correlations indicate that 

the concentrations of these elements in the suspended 

sediments may be linked to the buffering capacity of 

the water. However, it is not known how much of the 

correlation was due to association and how much of

the concentrations in the suspended sediment were 

actually caused by smaller buffering capacity.

Antimony, chromium, lead, nickel, silver, 

and zinc in suspended sediment positively correlated 

(p > 0.5) with total recoverable and dissolved phosphorus. This set of correlations indicates that large 

concentrations of some of the priority pollutants in 

suspended sediments are associated with large concentrations of phosphorus in water.

Correlations among elements in water and 

streambed sediment were calculated by means of 

three methods to clarify the relation of concentrations in water and the sediment. Streambed sediments were collected at 29 of the 40 sites where 

water samples were collected (table 6). Streambedsediment concentrations were correlated with median 

concentrations in water, 90th percentiles in water, and 

concurrent concentrations from water samples that 

were collected closest to the date when the streambedsediment samples were collected. Correlation coefficients from median concentrations in water indicate 

how the most typical concentrations in water from 

1987 through 1990 compared with concentrations in 

streambed sediment in 1987 (table 24). Correlation 

coefficients from the 90th percentiles of the water data 

indicate whether larger concentrations in water better 

reflect concentrations in the streambed sediment than 

median concentrations do (table 25). Lastly, correlation between concentrations from concurrent water 

samples and streambed sediment samples indicate 

whether relations among the water and sediment components are strongest if the time of sample collection 

is similar (table 26). Median and concurrent concentrations for many of the priority pollutants were below 

the minimum reporting level; if concentrations at more 

than 15 of the sites were below the minimum reporting 

level, the element was not included in the tables.

For some elements, correlation coefficients 

were similar regardless of the water data used. 

Correlation coefficients between streambed sediment 

and total recoverable and dissolved concentrations of 

boron, phosphorus, and strontium in water ranged 

from 0.58 to 0.68 regardless of whether the medians, 

90th percentiles, or concurrent samples were used.

For other elements, correlation coefficients 

depended strongly on the water data set used. For 

example, correlation coefficients among streambed 

sediment and total recoverable concentrations of 

copper, iron, lead, and nickel ranged from 0.51 to 

0.60 when the 90th-percentile water data were used;

74 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
however, correlation coefficients among these elements in streambed sediment and total recoverable 

concentrations were less or were not significant 

(p < 0.5 or p > 0.10) when the median and concurrent 

samples were used. Thus, large concentrations in 

water seem to correlate best with concentrations in 

streambed sediments for these elements. It must be 

noted, however, that correlations among median and 

concurrent concentrations in water and concentrations 

in streambed sediment were hindered by the many 

concentrations in water below the minimum reporting 

level.

Within-element correlations were not similar 

between streambed sediment and water and suspended 

sediment and water. Only nickel concentrations in 

streambed sediment and in suspended sediment correlated with total recoverable concentrations in water.

Correlations between streambed-sediment data 

and the 90th-percentile water data were observed 

among many different elements. For example, 

90th percentiles for total recoverable zinc correlated 

with chromium, copper, and molybdenum concentrations in streambed sediment at p = 0.51 to 0.56. Total 

recoverable copper concentrations correlated with 

aluminum, beryllium, boron, cobalt, copper, molybdenum, vanadium, and zinc in streambed sediments 

at p = 0.50 to 0.66. Total recoverable nickel correlated with aluminum, barium, beryllium, chromium, 

cobalt, copper, iron, molybdenum, vanadium, and zinc 

in streambed sediments at p = 0.50 to 0.87. Total 

recoverable lead correlated with selenium, beryllium, 

chromium, copper, mercury, molybdenum, nickel, 

vanadium, and zinc in streambed sediments at 

p = 0.50 to 0.72.

Similar to the suspended sediment, many 

priority pollutants in streambed sediments correlated 

with phosphorus concentrations in water. Of the 

three data sets used for water, the largest correlation 

coefficients were for concurrent dissolved and total 

recoverable phosphorus concentrations in water; and 

for beryllium, chromium, cobalt, copper, molybdenum, nickel, and zinc (p > 0.50) in streambed 

sediments. Chromium, copper, nickel, and zinc in 

streambed sediment correlated even more strongly 

with phosphorus in streambed sediment (p = 0.65 

to 0.80; Colman and Sanzolone, 1991). Large 

phosphorus concentrations in streambed sediment 

are associated with urban areas, as are many of the 

elements it significantly correlated with in streambed 

sediments. Phosphorus, however, was the only

urban-associated element that was always present in 

concentrations above its minimum reporting level in 

water. Thus, concentrations of phosphorus in water 

may serve as an indicator for the other urban-related 

elements typically found in concentrations below the 

current minimum reporting levels.

Correlations (p > 0.5) were observed between 

some element concentrations in biota and concentrations of elements in water and sediment components 

from the upper Illinois River Basin; however, correlations for boron, beryllium, chromium, lead, molybdenum, nickel, and silver were hindered by insufficient 

data or many data below the minimum reporting level. 

The variety of mollusk and plant species collected at 

sites resulted in insufficient data for any one species. 

In addition, limited overlap of sites sampled for 

organic carbon and element concentrations in suspended sediment precluded examination of correlations with element concentrations in tissues of all 

biota except common carp.

Correlations were found between concentrations 

of aluminum, barium, manganese, and strontium in 

biota and water (fig. 24). Aluminum concentrations 

in whole crayfish were found to be positively correlated with dissolved concentrations of this element in 

water (p = 0.90). Barium concentrations in whole 

crayfish were positively correlated with total recoverable barium in water (p = 0.98). Manganese 

concentrations in common carp and white sucker livers 

were positively correlated with concentrations of 

dissolved manganese (p = 0.57 and 0.55, respectively). 

Positive correlations were found between concentrations of strontium in common carp livers and in 

dissolved concentrations in water (p = 0.54). Most 

of the total recoverable strontium was in the dissolved 

phase, where it is available for uptake. Fish may be 

accumulating the strontium directly from the water and 

sediment or by ingestion of plants, which readily take 

up this element (Kabata-Pendias and Pendias, 1984).

Concentrations of arsenic in suspended sediment were positively correlated (p = 0.53) with 

concentrations of arsenic in common carp livers 

(fig. 25). The largest arsenic load and yield of the 

eight NAWQA fixed sites was found at the Fox River 

at Algonquin (site 89), an agricultural site, and arsenic 

concentrations in common carp livers from the Fox 

River tributaries were relatively large as a group. 

This relation indicates that arsenic in suspended 

sediments may be a source of arsenic in carp.

Correlations of Element Concentrations Among Water, Sediment, and Biota 75
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Figure 24. Relations of concentrations of selected elements in tissue to concentrations in water from the upper Illinois 

River Basin, 1989-90 (p = Spearman's ranked correlation coefficient).

76 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
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Correlations of Element Concentrations Among Water, Sediment, and Biota 77
Concentrations of cadmium in common 

carp livers and suspended sediment may also be 

correlated, although the correlation is confounded by 

two outliers (fig. 25). These two outliers represent 

the large concentrations in carp livers from the Fox 

River at Dayton (site 99) and the Iroquois River near 

Chebanse (site 28). Without these outliers, the correlation coefficient between cadmium in carp livers and 

in suspended sediment increases from p = -0.19 to 

0.74, indicating that large concentrations of cadmium 

in livers of common carp were positively correlated 

with large concentrations in suspended sediment. 

Other researchers have found positive correlations for 

concentrations of cadmium in fish livers and concentrations in water or sediment (Benoit and others, 1976; 

Boyer, 1984; Klaverkamp and others, 1991).

Positive correlations were found between some 

element concentrations in tissues and streambed sediments (fig. 26). Manganese concentrations in livers 

of white sucker were positively correlated with concentrations of this element in streambed sediment 

(p = 0.90). Strontium in common carp livers positively correlated with strontium in streambed sediment 

(p = 0.66). Although correlations were not evident, 

copper and nickel concentrations in biota from the 

North Branch Chicago River at Niles (site 45) reflected large concentrations of these elements in streambed sediments (tables Al and A3). Concentrations 

of copper in waterweed and crayfish from this site 

were the largest found in aquatic plants and crayfish 

(48.6 and 185 JJ-g/g, respectively). A composite 

sample of streambed sediments from this site contained 120 |lg/g copper, one of the three largest 

concentrations of copper found in the basin during 

the 1990 sampling. In addition, nickel concentrations 

in waterweed from this site were also the largest concentrations found in plants in the basin (36 J-lg/g), and 

nickel in streambed sediments from this site in 1990 

were at the second largest concentration found 

(53 flg/g) that year.

Negative correlations were found for copper 

and mercury (p = -0.58 and -0.71, respectively) 

between concentrations in common carp livers and 

in streambed sediment. As mentioned earlier, 

copper and mercury were positively correlated with 

each other in carp livers (p = -0.56). Two replicate 

carp-liver samples from Big Rock Creek (site 94) in 

1990 contained relatively large copper concentrations 

(130 and 179 J-lg/g). Yet, streambed sediment from

this small tributary to the Fox River had copper concentrations of 19 (ig/g, which is one of the smallest 

concentrations of copper in the Fox River Basin. 

Livers of common carp from the Des Plaines River 

above Brandon Road Dam at Joliet (site 58) had the 

smallest concentrations of copper and mercury in both 

sample years. Streambed sediments collected below 

the dam had the largest concentrations of these elements in 1990. Wiener and others (1984) found no 

significant relation between mercury concentrations in 

unsieved streambed sediments and common carp livers 

from the upper Mississippi River. Analysis of methylmercury in streambed sediment samples might aid 

interpretations of mercury concentrations in fish livers 

from the upper Dlinois River Basin. Harrison and 

Klaverkamp (1990) also found a negative correlation 

between concentrations of mercury in northern pike 

livers and unsieved lakebed sediments; copper concentrations in white sucker livers negatively correlated to 

copper concentrations in these sediments.

Concentrations of suspended organic carbon 

were positively correlated with concentrations of 

strontium in carp livers (p = 0.59) and were negatively correlated with cadmium, copper, and selenium 

(p = -0.63, -0.51, and -0.74, respectively) in carp 

livers (fig. 27). The outlier in the strontium data 

was from the Du Page River at Shorewood (site 69). 

The two outliers in the cadmium data represent the 

Iroquois River near Chebanse (site 28) and the Fox 

River at Dayton (site 99). Total organic carbon was 

positively correlated with concentrations of iron in 

carp livers (p = 0.54). Organic carbon compounds 

(such as humic and fulvic acids) are known to bind 

certain trace elements. This binding has generally 

been thought to render elements unavailable for uptake 

by biota (Spacie and Hamelink, 1985); however, 

Winner (1985) found that 7-day-old Daphnia pulex 

accumulated significantly more copper in the presence 

of humic acid than in an environment without humic 

acid. Recent work with two marine bivalves by 

Decho and Luoma (1994) indicates that organic carbon 

compounds may slightly enhance uptake of cadmium 

but reduce the availability of chromium. Positive 

correlations between trace elements in tissues and 

organic carbon concentrations in this study indicate 

that organic matter may have enhanced the uptake of 

an element to biota, whereas negative correlations

78 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
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MANGANESE IN STREAMBED SEDIMENT, 

IN MICROGRAMS PER GRAM

STRONTIUM IN STREAMBED SEDIMENT, 

IN MICROGRAMS PER GRAM

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COPPER IN STREAMBED SEDIMENT, 

IN MICROGRAMS PER GRAM

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MERCURY IN STREAMBED SEDIMENT, 

IN MICROGRAMS PER GRAM

Figure 26. Relations of concentrations of selected elements in tissue to concentrations in streambed sediment from 

the upper Illinois River Basin, 1989-90 (p = Spearman's ranked correlation coefficient).

Correlations of Element Concentrations Among Water, Sediment, and Biota 79
"T 

(/}

LULU

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go

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SUSPENDED ORGANIC CARBON, 

IN PERCENT

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800

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TOTAL ORGANIC CARBON, 

IN PERCENT

Figure 27. Relations of concentrations of selected elements in biota 

to organic carbon concentrations in the upper Illinois River Basin, 

1989-90 (p = Spearman's ranked correlation coefficient).

80 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
X X

</f(3 50 

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SUSPENDED ORGANIC CARBON, 

IN PERCENT

SUSPENDED ORGANIC CARBON, 

IN PERCENT

W W 1U

§ 

<S

11 6

SELENIUM CIN

IN MICROGRAMS O l\3*

, , , , | , , , , | , , , , | , , , , | , , , , | , , , , 

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SUSPENDED ORGANIC CARBON, 

IN PERCENT

Figure 27. Continued.

Correlations of Element Concentrations Among Water, Sediment, and Biota 81
might indicate that organic matter functioned as a 

binding agent that made an element less available to 

biota.

SUMMARY AND CONCLUSIONS

The U.S. Geological Survey, as part of a 

pilot National Water-Quality Assessment project, 

examined 22 major and trace elements in water, 

sediment, and biota in the upper Dlinois River 

Basin. The 22 elements include aluminum, 

antimony, arsenic, barium, beryllium, boron, 

cadmium, chromium, cobalt, copper, iron, lead, 

manganese, mercury, molybdenum, nickel, 

phosphorus, selenium, silver, strontium, vanadium, 

and zinc. The distributions and correlation of these 

elements in and among each of the three aquatic 

components were identified, although conclusions 

were hindered because of the large amount of concentration data below the minimum reporting level.

Several concentrations of the priority pollutants 

exceeded water-quality criteria at urban sites from 

1978 through 1986 and from 1987 through 1990, 

and the number of concentrations that exceeded these 

criteria were approximately the same at similar sites 

between these periods. The results from this study 

were not adequate to evaluate whether these concentrations above the criteria affect the propagation and 

distribution of biological communities. An ecological survey was done at the same time as the synoptic 

survey for biota. Results of the ecological survey 

may provide some insight into the relation between 

water chemistry and the health of aquatic organisms 

in the upper Illinois River Basin.

Mean annual loads and yields of urban-associated elements at urban sites typically were one order 

of magnitude larger than loads and yields of the same 

elements at agricultural sites. In the Chicago area, 

yields of lead from streams were similar to yields 

of lead from atmospheric deposition; however, yields 

of other priority pollutants, such as copper and zinc, 

were much greater in streams than in atmospheric 

deposition.

Although the Chicago area contains some of 

the most intensively used urban and industrial land, 

concentrations of many of the priority pollutants in 

water were below the minimum reporting level. This 

limited the amount of analysis that could be done 

with these pollutants. Better analytical techniques

with smaller minimum reporting levels would be 

necessary to evaluate the occurrence and distribution 

of trace elements in water, especially outside of urban 

areas. Minimum reporting levels for some elements 

were barely low enough to classify concentrations that 

were above water-quality criteria.

Correlations among elements in water were site 

specific for many elements, but correlations for 

grouped data from eight NAWQA fixed sites were 

similar to those for grouped data from 40 NAWQA 

and Illinois Environmental Protection Agency sites. 

Differences in correlations probably depended on the 

source of an element and on site-specific geochemical 

and biological processes. Total and dissolved 

concentrations correlated only for boron and strontium. Total and dissolved concentrations correlated 

for arsenic, barium, chromium, and nickel, but correlation coefficients differed significantly among sites. 

No correlation was found among dissolved and total 

recoverable concentrations for aluminum, copper, iron, 

and lead.

From 1978 through 1990, barium, boron, iron, 

manganese, and strontium concentrations in water 

decreased at many sites in the upper Illinois River 

Basin, and strontium concentrations in water increased 

at a number of other sites. Downward trends in 

streamflow were observed at two sites; these were not 

the same sites where concentrations of these elements 

decreased. More significant downward trends in 

streamflow were expected as a result of drought conditions from 1987 through 1989. Trends in barium and 

strontium concentrations are probably caused by 

changes in ground-water sources utilized as water 

supplies in the Fox and Du Page River Basins. The 

lack of expected downward trends in lead may be 

because of the release of lead from the stream sediments to the water column, which would maintain 

concentrations in water long after the initial source of 

the lead was removed.

All of the priority pollutants except arsenic 

were enriched in streambed sediments from urban 

areas relative to agricultural areas. The pattern of 

enrichment for many of these priority pollutants in 

streambed sediments continues for many miles down 

the Illinois River, although concentrations are reduced 

by sediment originating from the Fox and Kankakee 

River Basins. In addition, several of the priority 

pollutants were enriched in sediment from high-order 

streams relative to low-order streams. Correlation 

of the priority pollutants in sediments indicates that

82 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
streams contain a well-mixed variety of elements from 

municipal wastewater-treatment plants, combined 

sewer overflows in Chicago, industrial point sources, 

and urban runoff from streets, parking lots, and 

buildings.

Significant seasonal variations in element 

concentrations in suspended sediment indicate that the 

amount of elements transported in a stream depends on 

more that just the suspended-sediment concentration. 

Other geochemical or biochemical processes seem to 

affect the concentrations of elements in the suspended 

sediment. Understanding these processes is essential 

to developing adequate sediment-quality criteria.

The widespread effects of human activity on 

water resources in the upper Illinois River Basin made 

it difficult to identify reference sites where background 

concentrations of one or more elements could be found 

in all components, especially biota. Because of 

variation in concentrations among species and, at 

times, within different populations of a single species, 

information on background concentrations of elements 

in biota is critical in assessment of environmental 

effects on water quality. Some streams that were 

selected as reference sites on the basis of retrospective 

information and habitat were later identified as having 

elevated concentrations of several elements. Fortunately, concentrations of some elements were relatively small at one or more sites compared to other 

sites in the upper Illinois River Basin, even if those 

sites may have been enriched in other elements. This 

allowed for estimation of some "background" concentrations for the purposes of this study; however, these 

concentrations do not represent natural background 

concentrations because effects of human activity in the 

basin are widespread.

Element concentrations seem to be somewhat 

enriched in biota from several sites in the upper Illinois 

River Basin compared to other sites in and outside of 

the basin. In addition, biota from some urban sites, 

such as the North Branch Chicago River (site 45), 

North Shore Channel (site 46), Little Calumet River 

(site 53), and Salt Creek (site 38) were enriched with 

respect to more than one element. Studies of the 

effects of elevated concentrations of priority pollutants 

on biological development and diversity need to take 

into account the synergistic effects of these elements.

Whether elevated concentrations of some 

elements in biota from the upper Illinois River 

Basin resulted in toxicity to the biota is not known. 

Toxicity data from biota exposed to elements under

field conditions are uncommon and may not be applicable to biota from the basin. The inherent variability 

of natural systems and limitations in the ability to 

detect responses of biota to element exposures in 

nature has resulted in a lack of criteria for maximum 

tissue concentrations necessary to protect aquatic life 

(Luoma and Carter, 1991).

Correlations were observed between element 

concentrations in tissues of biota. Correlations of 

copper, mercury, and zinc concentrations were 

strongly positive with each other in white sucker and 

common carp livers; copper and zinc also were 

positively correlated in crayfish. In addition, 

aluminum, chromium, iron, and vanadium were 

positively correlated in crayfish. Correlations of 

these sediment-associated elements indicate a common 

source and mode of element accumulation in these 

biota.

Although statistical comparisons were not 

possible, patterns of element concentrations in biota 

indicate land-use relations. Arsenic was enriched in 

biota collected from sites representing agricultural land 

uses only, whereas chromium, lead, nickel, and strontium were enriched in biota collected from urban sites 

only. This pattern may indicate that these land uses 

are important sources of the element to biota in the 

basin. In contrast, elevated concentrations of barium, 

cadmium, copper, mercury, selenium, and zinc were 

observed at agricultural and urban sites.

Differences in element concentration among 

biota from sites in the upper Illinois River Basin 

support the collection of more than one species at a 

site in water-quality investigations. Concentrations 

of most elements were measurable in bivalves. In 

contrast, fish livers generally contained the smallest 

concentrations of all biota for aluminum, arsenic, 

barium, boron, chromium, manganese, strontium, and 

vanadium. Fish livers, however, generally contained 

the largest concentrations of copper, mercury, selenium, and zinc in biota from the basin. Fish livers 

also were adequate bioindicators of cadmium bioavailability, and carp livers generally contained the largest 

concentrations in biota. Whole crayfish may not be 

adequate bioindicators of cadmium for the upper 

Illinois River Basin. Submersed aquatic plants had 

fewer concentrations below the minimum reporting 

levels for element concentrations than all other biota 

collected in the basin. Caddisflies and wild celery 

from Salt Creek, an urban/industrial stream, accumulated concentrations of most elements well above

Summary and Conclusions 83
minimum reporting levels, including concentrations of 

some elements (chromium, nickel, and lead) that were 

near or below such levels in three other types of biota 

collected at this site. Thus, any one species of biota 

may not accumulate all elements of concern and, 

therefore, may not be a good bioindicator for some 

elements.

Results of sampling for water, sediment, and 

biota in the upper Illinois River Basin indicate that 

many major and trace elements are elevated or 

enriched in these components. Although concentrations of some priority pollutants were distinctly 

enriched in urban areas in all components, many of 

the pollutants were enriched in only the sediment 

component. In addition, arsenic concentrations in all 

components were enriched in agricultural areas.

Determining correlations among the three 

components was hindered by the amount of concentration data below minimum reporting levels. 

Correlations among elements in water and sediment 

differed among sites in many cases. In addition, 

correlations among biota and water and sediment were 

limited because of the number of different species 

sampled and insufficient amounts of data.

The largest arsenic concentrations in water, 

sediment, and biota were found at sites in the 

Kankakee River Basin. Agricultural use of arsenicbased chemicals (insecticides, herbicides, algicides, 

and desiccants) has resulted in the largest anthropogenic source of arsenic in the environment (Woolson, 

1975). Agriculture use, however, does not fully 

explain the larger concentrations of arsenic in the 

Kankakee River Basin because the Iroquois River, a 

tributary to the Kankakee River, drains an area with a 

greater percentage of agricultural land yet has smaller 

concentrations of arsenic in all three components. 

Arsenic concentrations in the Kankakee River seem 

to be affected by more than just the source of the 

arsenic. The predominance of arsenic in the 

Kankakee River Basin is enhanced by properties of the 

geochemical substrate, such as the particle size of 

sediments. The lack of fine-grained sediment in the 

Kankakee River Basin may have allowed more arsenic 

to be associated with iron and manganese coatings, 

which may have allowed the arsenic to become more 

bioavailable. Although concentrations of arsenic in 

water are below water-quality criteria, the apparent 

enrichment of arsenic in biota from the Kankakee 

River warrants further study.

The distribution of barium and strontium 

concentrations differed among the three components. 

For example, elevated strontium concentrations were 

found in water and biota in the Du Page and Fox 

River Basins, whereas concentrations of strontium in 

stream-bed sediment were elevated in the Fox River 

Basin but not in the Du Page River Basin. Large 

concentrations of barium in water were observed in 

the Fox and Du Page River Basins, but concentrations 

in sediments were not large in these basins. Elevated 

concentrations of barium and strontium in water seem 

to be related to ground-water sources in the Fox and 

Du Page River Basins.

Correlations of concentrations in streambed sediment and other components were limited by a lack of 

particle-size data to determine the proportion of finefraction sediments in total streambed sediments at a 

given location. Large concentrations of contaminants 

in fine-fraction sediments might be less available to 

biota and to the water column if these sediments were 

only a small percentage of the sediments at a location. 

Between-site differences in particle-size distribution of 

streambed sediments may help explain why correlations between concentrations of some elements in 

water, sediment, and biota were not observed in this 

study.

Phosphorus concentrations in water correlated 

with priority pollutants in streambed sediments. This 

relation means that elevated phosphorus concentrations in water could be used to indicate water that 

contains large concentrations of priority pollutants. 

This indication could be important where elements that 

are known to bioaccumulate are found below the 

minimum reporting level.

Significant correlations were observed among 

alkalinity and other buffer-related elements in water 

and priority pollutants in suspended sediment and 

streambed sediment. Thus, the buffering capacity of 

the water seems to have affected concentrations of 

priority pollutants in the sediment.

Positive and negative correlations were 

observed among water or sediment and biota for some 

elements. Concentrations of aluminum and barium in 

crayfish positively correlated with concentrations of 

these elements in water and concentrations of manganese and strontium positively correlated with concentrations of these elements in common carp livers. 

Concentrations of arsenic and possibly cadmium in 

suspended sediment were positively correlated with 

concentrations of these elements in common carp

84 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
livers. Manganese in white sucker livers and 

strontium in common carp livers were positively correlated with concentrations of these elements in 

streambed sediments. These relations indicate that 

suspended and streambed sediments may be important 

sources of these elements to biota. Negative correlations were found between concentrations of copper and 

mercury in common carp livers and in streambed 

sediment. Concentrations of suspended organic 

carbon were positively correlated with concentrations 

of strontium in carp livers and were negatively correlated with cadmium, copper, and selenium in carp 

livers. Total organic carbon concentration positively 

correlated with iron concentrations in carp livers.

The small number of correlations found 

between element concentrations in tissues of biota and 

other components in this study emphasizes that water 

and sediment cannot be used as surrogates for biota, 

that concentrations in biota cannot presently be determined from concentrations in these components, and 

that bioaccumulation must be measured directly. 

This is because of the complex variety of chemical, 

physical, and biological variables affect the bioavailability of elements from water and sediment. Biota 

have been effectively used in several water-quality 

studies in the upper Illinois River Basin and elsewhere 

as indicators of bioavailability and as a complementary 

line of evidence with water and sediment data in interpretations of anthropogenic effects (Phillips, 1980; 

Steffeckand Striegl, 1989).

Whereas element concentrations in water are 

instantaneous, concentrations in sediments and biota 

may provide indicators of water quality that are 

integrated over time. At sites where ambient 

concentrations fall below current analytical minimum 

reporting levels for water, concentrations in sediment 

and biota can provide valuable water-quality information. In the upper Illinois River Basin, total 

recoverable and dissolved concentrations of a number 

of elements in water were commonly near or below 

minimum reporting levels in water but were measurable, and at times elevated, in sediment and biota. 

These elements included the highly toxic priority 

pollutants arsenic, selenium, and zinc. Concentrations of mercury in sediment and biota were 

measurable and distinctly different among sites, even 

though many observations were below the minimum 

reporting levels for total recoverable and dissolved 

mercury in water. For these reasons, a combination 

of information from various components is clearly the

optimum for achieving the most complete understanding possible of water quality in the upper Illinois 

River Basin.

CONSIDERATIONS FOR FUTURE 

NATIONAL WATER-QUALITY 

ASSESSMENT STUDIES

Results from the analysis of major and trace 

elements in water, sediment, and biota from the pilot 

NAWQA study of the upper Illinois River Basin 

indicate that the following considerations are 

important for future NAWQA studies.

Sampling Design

1. Objectives. Such objectives would 

ideally be set as early as possible in the project to 

maximize efficiency of sampling and usefulness of the 

data. Quantitative analysis of data collected in the 

pilot NAWQA synoptic surveys of sediment and biota 

in the upper Illinois River Basin was restricted because 

of multiple objectives in the design of the surveys.

2. Overlap with data-collection network. 

The number of sites that overlap between surveys of 

different components must be carefully determined if 

the objectives of the project include (a) statistical 

comparisons of differences in constituents among 

water, sediment, and biota and (b) description of the 

accumulation and fate of the constituents through the 

aquatic system.

3. Selection of reference sites. Review of 

retrospective data, information from local experts, and 

onsite reconnaissance are critical to selection of 

reference sites. Use of more than one reference site 

helps to ensure that background concentrations of all 

elements of interest are adequately identified.

4. Number of species and organisms in 

samples. Comparability of biotic samples is 

enhanced if the number of species of biota collected 

in a basin (or program) is minimized and at least five 

individual organisms are included in each composite. 

Best results are obtained when individuals of a species 

are similar in size among sites and replicate composite 

samples are collected at a certain number of sites. 

These considerations have been addressed for the 

design of future NAWQA studies by Crawford and 

Luoma(1993).

Considerations for Future National Water-Quality Assessment Studies 85
5. Types of biota. Ideally, at least two 

species of different types of biota would be collected at 

each site whenever possible. This strategy has been 

recommended for at least 50 percent of all sites in 

future NAWQA studies to aid assessment of the 

bioavailability of all elements that may be of concern 

(Crawford and Luoma, 1993).

6. Collection of biota by subbasin or 

ecoregionu Collection of the same species of biota 

from at least five sampling locations in each subbasin 

or ecoregion would allow statistical comparison of 

element concentrations in biota among either 

subbasins or ecoregions in the basin.

Field and Laboratory Methods

1. Consistency in sampling methods. 

Although project teams commonly think of potential 

improvements in methods during a project, consistency in sampling methods is essential for data 

comparability. For example, sediments collected 

during the biology synoptic sampling should be the 

same as those used during the sediment synoptic 

sampling if the data are to be compared.

2. Consideration of sediment particle

size. If the amount of an element in the sediment is 

of interest, then particle-size analysis could be considered for identifying the amount of the sample in the 

fine fraction. Particle-size analysis is inexpensive 

compared to other chemical analyses, and it is almost 

always useful in interpretation of element concentrations, even if simple verification of the presence of the 

element is the only objective of the sampling strategy.

3. Partial digestion of sediment samples. 

Compared with total digestions, partial digestions 

provide more information about the concentrations of 

elements in adsorbed materials, which are important 

for assessing the amount that may be transported from 

the sediment to the water column. Partial digestions 

also are more useful for assessing the amount of an 

element that is available for biological uptake.

4. Minimum reporting levels. Use of the

most appropriate and state-of-the-art laboratory 

methods is necessary to achieve adequate minimum 

reporting levels and minimize the number of "lessthan" values in a data set.

Ancillary Data

1. Composition of soil and rock. Collection of comparable background information on concentrations of elements in soils, glacial materials, and 

bed-rock in the study area would be useful in classifying concentrations of elements in stream sediments. 

In the upper Illinois River Basin, background concentrations identified in previous studies could not be 

directly compared to samples collected during the 

NAWQA study.

2. Geographic data and analysis. A

geographic information system can be useful for 

analyzing large data bases and for integrating and 

displaying information from a wide variety of sources. 

Useful maps include, but are not limited to, land use, 

point sources, soils, surficial geology, and bedrock 

geology.

3. Composition of ground water. If ground 

water significantly contributes to base flow, data on 

concentrations of major and trace elements in this 

component would be valuable for interpretation of 

element concentrations in the surface-water column. 

Analysis should be done to determine which sites (if 

any) can be eliminated and where new sites (if any) 

should be added. In the full-scale NAWQA program, 

surface-water and ground-water components will be 

integrated.

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and Standards, 440/5-86-001, 453 p.

 1988, National Interim primary drinking water

regulations, U.S. Code of Federal Regulations, title 40, 

parts 100-149, p. 530-587.

U.S. Food and Drug Administration, 1984, Shellfish

sanitation interpretation action levels for chemical 

and poisonous substances, June 21, 1984, Washington, 

D.C., Shellfish Sanitation Branch.

Wiener, J.G., Jackson, G.A., May, T.W., and Cole, B.P., 

1984, Longitudinal distribution of trace elements 

(As, Cd, Cr, Hg, Pb, and Se) in fishes and sediments 

in the upper Mississippi River, in Weiner, J.G., 

Anderson, R.V., and McConville, D.R., eds., 

Contaminants in the upper Mississippi River: 

Boston, Mass., Butterworth Publishers, p. 139-170.

Williams, S.L., Aulenbach, D.B., and Clesceri, N.L., 1974, 

Sources and distributions of trace metals in aquatic 

environments, in Rubin, A.J., ed., Aqueousenvironmental chemistry of metals: Ann Arbor, 

Mich., Ann Arbor Science Publishers, p. 77-128.

Willman, H.B., 1973, Geology along the Illinois

Waterway a basis for environmental planning: 

Illinois State Geological Survey Circular 478, 48 p.

Willman, H.B., and Frye, J.C., 1970, Pleistocene

stratigraphy of Illinois: Illinois State Geological 

Survey Bulletin 94, 204 p.

Willman, H.B., Atherton, E., Buschbach, T.C., 

Collinson, C., Frye, J.C., Hopkins, M.E., 

Lineback, J.A., and Simon, J.A., 1975, 

Handbook of Illinois stratigraphy: Illinois 

State Geological Survey Bulletin 95, 261 p.

Winchester, J.W., and Nifong, G.D., 1971, Water pollution 

in Lake Michigan by trace elements from pollution 

aerosol fallout, in Water, Air, and Soil Pollution 1: 

Dordrecht, Holland, D. Reidel Publishing Company, 

p. 50-64.

References Cited 93
Windom, H.L., Byrd, J.T., Smith, R.G., Jr., and Huan, Feng, Woolson, E.A., ed., 1975, Arsenical pesticides: American 

1991, Inadequacy of NASQAN data for assessing Chemical Society Symposium Series, v. 7, 176 p. 

metal trends in the Nation's rivers: Environmental 

Science & Technology, v. 25, no. 6, p. 1137-1142.

Winner, R.W., 1985, Bioaccumulation and toxicity of

copper as affected by interactions between humic acid 

and water hardness: Water Research, v. 19, no. 4, 

p. 449^55.

94 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
TABLES 1-26
Table 1 . Representative concentrations of selected elements from various background sources

[mg/kg, milligrams per kilogram; mg/L, milligrams per liter; O.X indicates order of magnitude known; <, less than; --, no data]

ijor andTrac

e Elements inW;

HI

1

3

0)

a

00

f

(O

Representative concentrations

United States

Element

Aluminum 

Antimony 

Arsenic

Barium 

Beryllium

Boron 

Cadmium

Chromium

Cobalt

Copper

Iron 

Lead

Manganese 

Mercury 

Molybdenum

Nickel

Phosphorus 

Selenium

Silver

Strontium

Vanadium

Zinc 

Carbon,total organic

Carbonate 

rocks1 

(mg/kg)

1,700-20,000

7.2 

.74-2.5

5.6-160 

9.X

29-31 

9.035

2.7-29

1.3-71

.84-12

1,100-21,000 

4-18

83-910 

.022-.03 

.79

2.3-16

40-600 

.16-.31

.X

100-990

3.9^0

6.3-24 

1,000-2,800

Sandstone 

and shale1 

(mg/kg)

4,300-92,000 

9.4-1.5 

1.1-9.0

38-510 

.80-1.7

18-110 

9.OX-.3

2.0-130

1.1-13

1.2-130

900-45,000

5-24

29^20 

.0079-.34 

.2-26

1.2-110

10-100 

.09-. 11

.18

13-220

5.5^00

5.2-82 

2,700-3,500

Soils and

surficial 

material1 

(mg/kg)

9,000-65,000 

5.5-13.0

63-810 

.76-1.3

18-63 

9<.5

11-78

1.0-14

8.7-39

4,700-43,000 

2.6-25

61-1,100 

.045-. 160

1.8-23

40-800 

.27-.T4

3.6-160

15-110

25-68 

7,000-28,000

Plant ash2 

(mg/kg)

200-39,000

15-11,000 

.64-2.0

37-600 

.37-20

42-22

.50-400

21-270

600-9,300 

7.1^80

96-14,000 

.76-20

.81-130

7,100-220,000 

.01-42

14-5,300

2.6-23

170-1,900

Upper 

Illinois River 

Basin

Bulk 

precipitation3 

(mg/L)

<0.0001-.001

.003-.005 

<.0005

<.001-.023

<.003-.004

<.01-.04

.013-.049 

.003-.006

.009-02 

<.0001-.0001

<001-.011

<.0001

.0017-.0038

<.006

.009-.029

Upper Mississippi Riv

Basin

Total 

recoverable4 

(mg/L)

<0.0001-.015

0-.01

O-.ll

0-.06

0-.8

.24-23 

0-.32

.02-1.5 

0-.0015

_

0-.013

-

_

.01-.15

Dissol

(mg/

<0.0001

0-.00

0-.0

0-.00

0-.07

0-.5 

0-4

0-1.

0-.00

..

0-.00

--

_

0-.2

'Data from Conner and Shacklette (1975) unless otherwise noted.

2Data from Conner and Shacklette (1975).

3Datafrom Peters and Bonelli (1982).

4Data from Britton and others (1983).

5Data from Mathis and Cummings (1970) unless otherwise noted. Data from Mathis and Cummings (1970) are from three nonindustrial-use tributaries to t

6Data from Mathis and Cummings (1970).

7Data from Turekian (1971). Data for the world.

8Data from Kelly and Kite (1984).

9Data from Gilkeson and others (1977). Data for Ogle County, 111.
Table 2. Concentrations of selected elements in materials related to domestic sewage treatment in the upper 

Illinois River Basin

[All concentrations in milligrams per liter. No data available for aluminum, cobalt, molybdenum, strontium, and vanadium. 0, below the 

minimum reporting level; , no data available]

Concentration range of 

monthly means of final 

effluent for Calumet, 

West-Southwest, and 

North Side treatment 

Element plants, 1988

Concentration range of

annual means of raw

sewage entering Calumet,

West-Southwest, and North

Side treatment plants, 1989

Concentration range

of annual means of

Calumet TARP1 raw

sewage, 1988-90

Antimony 

Arsenic

Barium

Beryllium

Cadmium

Chromium

Copper 

Iron

Lead

Manganese 

Mercury 

Nickel

Phosphorus 

Selenium

Silver

Zinc

0 

0

0

0

0-.03

.06-.33

.07-.23 

.8-^.1

.01-.09

.05-. 19 

.0001-.00297 

0

3.2-12.5 

0

0-.01

.1-.8

0 

0

0

0

.01-.02

.02

.04-.05

2.2-2.4

.2-.4

.10-.11 

.00013-.00016 

0

1.93-3.55 

0-.02

0

.1-1.9

0-0

0-.04

--

0-.02

0-.05

0-.10 

0-.42

0-.03

0-.13 

0-.00021 

0-.06

.175-3.19 

O-.ll

0-0

0-.15

*TARP refers to the Chicago Tunnel And Reservoir Plan (Metropolitan Water Reclamation District of Greater Chicago, 1990).

Table 3. Total releases of selected elements from wastewater-treatment plants in the Chicago Metropolitan 

area and in Illinois, and percentage of release from Illinois to the atmosphere and to streams

[Data are from Illinois Environmental Protection Agency (1991). No data available for beryllium, boron, iron, and strontium. Other releases 

are to wastewater-treatment plants, underground injection, land or other offsite transfers, or a combination thereof; <, less than]

Element

Total releases 

(pounds)

Chicago 

metropolitan area Illinois

Percentage of Illinois 

_____releases_____ 

To surface

water To air

Aluminum and related compounds

Antimony and related compounds

Arsenic and related compounds

Barium and related compounds

Cadmium and related compounds

Chromium and related compounds

Cobalt and related compounds

Copper and related compounds

Lead and related compounds

Manganese and related compounds

Mercury and related compounds

Molybdenum and related compounds

Nickel and related compounds

Selenium and related compounds

Silver and related compounds

Vanadium and related compounds

Zinc and related compounds

772,602

4,688

3,969

226,509

13,388

868,613

12,670

2,012,288

709,637

2,493,419

0

19,113

992,407

5,655

2,996

0

3,599,814

3,164,323

24,368

23,806

4,945,174

40,250

1,900,204

34,454

3,288,829

2,171,248

7,454,842

4

19,113

1,895,396

5,655

2,996

93

19,682,493

<!

<1

<1

<1

0

1

3

1

1

<l

0

0

<1

0

0

0<l

6

12

13

1

22

4

10

6

4

2

100

19

6

18

67

100

5

Table 2 97
Table 4. Freshwater acute and chronic water-quality criteria, fish-consumption advisory levels, and Maximum 

Contaminant Levels for primary drinking water regulations for 15 elements

[ *, insufficient data to develop criteria value presented is lowest observed effect level; +, criteria are dependent on hardness of water 

(100 milligrams per liter used for table); MCL, Maximum Contaminant Level; mg/L, milligrams per liter; ng/L, nanograms per liter; 

ug/L, micrograms per liter; , no criteria or level available]

Freshwater-quality 

criteria1

Element

Antimony

Arsenic

Arsenic(V)

Arsenic(ni)

Barium

Cadmium

Beryllium

Chromium(VI)

Chromium(in)

Copper

Iron

Lead

Manganese

Mercury

Nickel

Selenium

Silver

Zinc

Priority 

pollutant

Yes

Yes

Yes

Yes

No

Yes

Yes

Yes

No

Yes

No

Yes

No

Yes

Yes

Yes

Yes

Yes

Carcinogen

No

Yes

Yes

Yes

No

No

Yes

No

No

No

No

No

No

No

No

No

No

No

Acute 

(U9/L)

*9,000

*850

360

+3.9

*130

16

+1,700

+18

__

+82

2.4

+1,400

260

+4.1

+120

Chronic 

(ug/L)

* 1,600

*48

190

+1.1

*5.3

11

+210

+12

1,000

+3.2

.012

+160

35

.12

110

Fish 

consumption 

advisory levels 

(units as noted)

45 mg/L

17.5 ng/L

117 mg/L

3,433 mg/L

__

lOOjig/L

146mg/l

lOOjig/L

_

_

~

Drinking 

water 

MCL2 

(mg/L)

0.05

1.0

.01

.05

.05

1.3

.3

.015

-

.002

.01

.05 35.0

'U.S. Environmental Protection Agency, 1986. 

2U.S. Environmental Protection Agency, 1988. 

3Recommended goal, not legally enforceable.

Table 5. Guidelines for pollutional classification of sediments

[All values in micrograms per gram; <, less than; >, greater than; --, data not available; USEPA, U.S. Environmental Protection Agency; 

OMEE, Ontario Ministry of Environment and Energy]

Element

Arsenic

Barium

Cadmium

Chromium

Copper

Iron

Lead

Manganese

Mercury

Nickel

Zinc

Nonpolluted

<3

<20

USEPA1

Moderately 

polluted

3-8

20-60

Lower limits not established

<25

25

<17,000

<40

<300

25-75

25-50

17,000-25,000

40-60

300-500

OMEE2

Heavily 

polluted

>8

>60

>6

>75

>50

>25,000

>60

>500

>1 is unacceptable for open lake disposal >1

<20

<90

20-50

90-200

>50

>200

Lowest effect 

level

6

.6

26

16

2

31

460

.2

16

120

Severe effect 

level

33

10

110

110

4

250

1,100

2

75

820

Guidelines from U.S. Environmental Protection Agency, 1977. 

2 Guidelines from Persaud and others, 1993.

98 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Table 6. Sites sampled

[BS, streambed sediment; SS,

in the upper Illinois River Basin for elements in water, sediment, and biota, 1978-90

suspended sediment; USGS, U.S. Geological Survey; IEPA, Illinois Environmental Protection Agency; , not determined]

Site 

number 

(fig. 5)

2

6

9

11

14

20

22

24

25

27

28

31

32

33

34

35

USGS 

station 

number

05515480

05517120

05517725

05518000

05520500

05525000

05525500

05525555

05525570

05525680

05526000

05527500

05527800

05528000

05529000

05530590

Site name

Mill Creek at Hwy 39 near Kingsford Heights, Ind.

Pitner Ditch at State Highway 8 near La Crosse, Ind.

Crooked Creek at 100 South Road near Wanatah, Ind.

Kankakee River at Shelby, Ind.

Kankakee River at Momence, 111. 1

Iroquois River at Iroquois, 111.

Sugar Creek at Milford, 111.

Spring Creek near Delrey, 111.

Spring Creek at Road 730 East near Onarga, 111.

Langan Creek at Road 1300 East near Clifton, 111.

Iroquois River near Chebanse, 111. 1

Kankakee River near Wilmington, 111.

Des Plaines River at Russell, 111.

Des Plaines River near Gurnee, 111.

Des Plaines River near Des Plaines, 111.

Des Plaines River near Schiller Park, 111.

Latitude 

longitude

41°27'04"

86°44'14"

41°19' 13"

86°50'48"

41°25'12"

86°57'46"

41°10'58"

87°20'33"

41°09'36"

87°40'07"

40°49'25"

87°34'55"

40°37'50"

87°43'25"

40°37'49"

88°00'22"

40°41'52"

87°59'09"

40°58'08"

87°53'04"

41°00'32"

87"49'27"

4r20'48"

42°29'22"

87°55'32"

42°20'39"

87°56'18"

42°04'55"

87°53'25"

41°57' 11"

Predominant 

land use

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Urban

Urban

Drainage 

area 

(square miles)

_

1,779

2,294

686

446

47.4

146

94.2

2,091

5,150

123

232

360

444

87°51'15"
£ Table 6. Sites sampled in the upper Illinois River Basin for elements in water, sediment, and biota, 1978-90 Continued 

o

a> o'

B> 

i.

H

B>

% (D

m(D*

1

V)

5'

a

5

Ia.

3

I

B>

Q.

00o'

?

 L

(O

-J

rto

0

Site 

number 

(fig- 5)

38

39

40

42

43

45

46

49

50

52

53

54

55

56

57

58

60

62

63

USGS 

station 

number

05531500

05532000

05532500

05534050

05534500

05536000

05536107

05536195

05536275

055363252

05536366

05536700

05536995

05537000

05537980

05538008

05539000

05539900

05540066

Site name

Salt Creek at Western Springs, 111.

Addison Creek at Bellwood, 111.

Des Plaines River at Riverside, 111. 1

Des Plaines River at Lockport, 111.

North Branch Chicago River at Deerfield, 111.

North Branch Chicago River at Niles, 111.

North Shore Channel at Touthy Avenue at Chicago, 111.

Little Calumet River at Munster, Ind.

Thorn Creek at Thornton, 111.

Little Calumet River at Halsted Avenue at Harvey, 111.

Little Calumet River at Calumet Park, 111.

Calumet Sag Channel at Sag Bridge, 111.

Chicago Sanitary and Ship Canal at Romeoville, 111. 1

Chicago Sanitary and Ship Canal at Lockport, 111.

Des Plaines River at Route 53 at Joliet, 111.

Des Plaines River above Brandon Road Dam at Joliet, 111.

Hickory Creek at Joliet, 111.

West Branch Du Page River near West Chicago, 111.

West Branch Du Page River at Mack Road near

West Chicago, Dl.

Latitude 

longitude

41°49'35"

87°54'00"

41°52'48"

87°52'07"

41°49'20"

87°49'15"

41°35'47"

88°04'07"

42°09'10"

87°49 ' 07 "

42°00'44"

87°47'45"

420 00'42"

87°42'37"

4r34'07"

87°31'18"

41 0 34'05"

87°36'30"

41°37'45"

87°38'30"

4r39'26"

87°38'29"

41°41'45"

87°56'11"

41°38'26"

88°03'38"

41°34'11"

88°04'42"

41°32'12"

88°04'57"

4r30'24"

88°05'49"

41°31'10"

88°04'10"

41°54'39"

88°10'44"

41°50'33"

88°11'56"

Predominant 

land use

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Urban

Drainage 

area 

(square miles)

115

17.9

630

700

19.7

100

90.0

104

254

24.3

389

739

740

1,502

1,506

107

28.5

80.6
Table 6. Sites sampled in the upper Illinois River Basin for elements in water, sediment, and biota, 1978-90 Continued

Site 

number 

(fig. 5)

64

65

66

67

69

72

74

76

78

80

81

84

86

88

89

90

51 91 o-

(D

o> 92

USGS 

station 

number

05540095

05540210

05540258

05540290

05540500

05541710

05542000

05543500

05544090

05544908

05544950

05546700

05548280

05549600

05550000

05550500

05551000

05551540

Site name

West Branch Du Page River near Warrenville, 111.

East Branch Du Page River at Route 34 Bridge at

Lisle, El.

East Branch Du Page River at Naperville, 111.

Du Page River near Naperville, 111.

Du Page River at Shorewood, 111. 1

Aux Sable Creek near Morris, 111.

Mazon River near Coal City, 111.

Illinois River at Marseilles, 111. 1

Mukwonago River at Marsh Road near Mukwonago, Wis.

Honey Creek at Bell School Road near East Troy, Wis.

Honey Creek at Hill Valley Road near East Troy, Wis.

Fox River near Channel Lake, 111.

Nippersink Creek near Spring Grove, 111.

Fox River at Burtons Bridge, 111.

Fox River at Algonquin, 111. 1

Poplar Creek at Elgin, 111.

Fox River at South Elgin, 111.

Fox River at Montgomery, 111.

Latitude 

longitude

41°49'22"

88°10'23"

41°48'02"

88°04'53"

41°42'52"

88°06'44"

41°41'24"

88°09'58"

41°31'20"

88°11'35"

41°25'02"

88°20'51"

4ri7'10"

88°21'35"

41°19'37"

88°43'03"

42°51'17"

88°23'44"

42°47'43"

88°19'15"

42°47'03"

88°18'33"

42°28'45"

88° 10'42 "

42°26'37"

88°14'51"

42° 16 '44"

88°13'31"

42°09'59"

88° 17' 25 "

42°01'35"

88° 15 '20"

41°59'40"

88° 17 '38"

41°43'46"

88°20'19"

Predominant 

land use

Urban

Urban

Urban

Urban

Urban

Agricultural

Agricultural

Agricultural

and urban

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

Agricultural

and urban

Urban

Agricultural

and urban

Agricultural

and urban

Drainage 

area 

(square miles)

90.4

51.4

--

220

324

172

455

8,259

871

192

1,278

1,403

35.2

1,556

1,732
£ Table 6. Sites sampled in the upper Illinois River Basin for elements in water, sediment, and biota, 1978-90 Continued

s

"o"

Q)

3

Q.

0

<Dm

1

5*

CO5'

21

5f

1Q.

»

2.

Q)

3

0.

03

a

sr

Site

number

(fig. 5)

93

94

96

97

99

USGS

station

number

05551700

05551933

05551995

05552200

05552500

Site name

Blackberry Creek near Yorkville, 111.

Big Rock Creek above Henning Road near Piano, 111.

Somonauk Creek at Sheridan, 111.

Indian Creek near Harding, 111.

Fox River at Dayton, 111. 1

Latitude

longitude

41°40'18"

88°26'29"

41 "41 '58"

88°30'30"

41°32'37"

88°41'12"

41°30'50"

88°47'50"

41°23'12"

88°47'26"

Predominant

land use

Agricultural

and urban

Agricultural

Agricultural

Agricultural

Agricultural

and urban

Drainage

area 

(square miles) 

70.2 

83.3 

2,642 

'National Water-Quality Assessment fixed site.
Table 7. Element concentrations that exceeded U.S. Environmental Protection Agency freshwater chronic and acute

criteria for total recoverable concentration, 1978-86

[Format: number of observations - number of times chronic criteria was exceeded - number of times acute criterion was exceeded. NA, criteria not

available; No obs., no observations; U.S. Environmental Protection Agency criteria do not exist for elements not shown, except nickel, which had no

exceedances]

Site 

number 

(fig. 5)

14

20

22

28

31

32

33

34

35

38

39

42

43

45

46

27

54

56

57

60

62

64

65

67

69

72

74

76

84

86

88

89

90

91

92

93

96

99

Element

Cadmium

44- 4- 0

31- 3- 0

33- 7- 0

30- 5- 0

73- 6- 0

43- 3- 0

57-16- 1

42- 2- 0

49- 1- 0

46- 3- 0

41- 4- 2

42- 2- 0

32- 2- 0

49- 1- 1

37- 2- 0

27- 2- 0

44- 2- 0

45- 3- 0

40- 3- 0

42- 4- 0

41- 5- 0

73- 4- 0

38- 1- 0

No obs.

No obs.

No obs.

No obs.

74- 8- 0

48- 1- 0

42- 2- 0

37- 1- 0

No obs.

No obs.

39- 1- 0

46- 2- 0

33- 2- 0

38- 1- 0

48- 3- 0

Chromium

94- 7- 4

55- 2- 1

55- 8- 3

57- 5- 0

91- 6- 6

72- 3- 1

89-10- 7

67- 3- 0

87- 4- 0

89- 9- 6

56-16-14

67- 7- 1

65- 4- 3

90- 5- 4

68- 4- 4

54- 6- 0

63- 6- 5

94-25-11

41-15- 5

56- 4- 2

54- 4- 1

86-10- 6

62- 3- 1

62- 2- 1

61- 1- 1

56- 2- 0

61- 1- 1

102-39-31

97- 2- 1

65- 4- 2

54- 2- 2

65- 1- 0

85- 5- 1

61- 2- 0

90- 4- 3

60- 1- 1

50- 1- 1

95- 5- 2

Copper

No obs.

No obs.

33-1- 1

29- 1- 1

77- 3- 0

42-0- 1

75- 1- 0

42- 1- 0

49- 5- 2

46-7- 5

46-7- 5

No obs.

32-1- 1

48-7- 6

37-3- 1

No obs.

45-3- 2

45- 1- 0

40-4- 1

42-2- 1

No obs.

73- 2- 0

No obs.

No obs.

No obs.

No obs.

No obs.

80-18- 8

48- 5- 3

42- 3- 1

No obs.

38- 1- 1

No obs.

40- 1- 0

46- 3- 3

No obs.

No obs.

48- 4- 3

Iron

61-36-NA

56-35-NA

57-30-NA

61-40-NA

93-35-NA

67-33-NA

98-47-NA

66-4 1-NA

58-34-NA

62-37-NA

62-37-NA

60-3 1-NA

64-42-NA

60-23-NA

40-28-NA

54-18-NA

53-33-NA

61- 9-NA

41- 7-NA

53-14-NA

52-34-NA

95-57-NA

59-20-NA

61-21-NA

61-22-NA

75-20-NA

93-36-NA

102-49-NA

61-16-NA

65-18-NA

52- 5-NA

65- 9-NA

94-3 1-NA

60-10-NA

61-24-NA

63-38-NA

50-12-NA

94-35-NA

Lead

44- 1- 0

31- 1- 0

No obs.

30- 1- 0

74-16- 0

No obs.

75-17- 2

No obs.

49- 1- 0

46- 2- 0

42- 5- 3

No obs.

No obs.

49- 1- 1

No obs.

No obs.

45- 2- 0

No obs.

40- 1- 0

42- 1- 0

No obs.

73-13- 0

39- 1- 0

43- 1- 0

No obs.

No obs.

No obs.

71-16- 0

No obs.

42- 1- 0

No obs.

39- 1- 0

55-17- 0

40- 1- 0

No obs.

No obs.

No obs.

No obs.

Mercury

87- 8- 1

No obs.

No obs.

No obs.

66-17- 0

No obs.

17- 9- 0

19- 1- 0

82-14- 0

88- 5- 0

No obs.

No obs.

12- 2- 0

89-11- 0

68-23- 0

8- 2- 0

59- 7- 0

92-10- 0

42- 2- 0

12- 1- 0

10- 1- 0

14- 8- 0

No obs.

No obs.

19- 2- 0

73- 4- 0

84-8-0

94-32- 0

86-10- 1

No obs.

No obs.

14- 1- 0

10- 6- 0

16- 1- 0

86- 4- 0

No obs.

No obs.

93- 8- 0

Silver

44- 7- 0

31- 5- 0

33- 6- 0

30- 9- 0

51- 6- 0

42- 3- 0

44- 4- 0

41- 1- 0

48- 2- 0

46- 3- 0

41- 2- 0

No obs.

32- 1- 0

49- 2- 1

36- 4- 0

No obs.

44- 2- 0

No obs.

40- 4- 0

42- 4- 0

41- 4- 0

42- 3- 0

39- 4- 1

43- 2- 0

43- 2- 0

No obs.

23- 1- 0

62- 6- 0

48- 5- 0

42- 6- 0

37- 2- 0

39- 1- 0

22- 0- 2

39- 2- 0

45- 2- 0

33- 3- 0

38- 5- 0

48- 2- 0

Zinc

44- 1- 1

No obs.

33- 2- 1

No obs.

No obs.

41- 2- 2

75- 1- 0

No obs.

No obs.

45- 2- 2

41- 4- 3

41- 1- 1

No obs.

49- 2- 2

No obs.

No obs.

44- 7- 7

45- 1- 0

40- 3- 1

No obs.

No obs.

72- 1- 1

No obs.

No obs.

No obs.

22- 1- 1

No obs.

58- 2- 1

48- 2- 2

No obs.

No obs.

No obs.

No obs.

38- 1- 1

45- 1- 1

33- 1- 1

36- 2- 1

47- 1- 1

Table 7 103
Table 8. Comparison of total recoverable yields of selected elements in water and in atmospheric 

deposition in the upper Illinois River Basin

[AH yields in tons per square mile per year. Numbers in parentheses following stream names are site numbers. If a range of numbers 

is given for yields, the numbers represent the range in values when censored values were replaced with 0 and the minimum reporting level. 

 , no data available]

Yields (total recoverable)

Urban

Element

Aluminum

Cadmium

Cobalt

Copper

Iron

Lead

Manganese

Zinc

Atmospheric

deposition1

0.4

.0008

<.001

.007

.20

.05

.05

.07

Chicago Sanitary

and Ship Canal

(55)

1.4

.0045

.03-.04

2.2-2.4

.06-.07

.19

.4-.5

Thorn

Creek

(50)

3.5

.001-.006

.01-.03

4.4-4.7

.02-.05

.14

.008-. 11

Des Plaines

River

(40)

1.6

.0006

.02-.03

2.3

.02-.04

.10

.09-. 11

Addison

Creek

(39)

8.8

.0006-.004

.03

3.1

.02-.06

.18

.15-.66

Agricultural

Iroquois

River

(28)

3.5

3.0001-.0003

.007-.009

3.8-4.5

.002-.008

.08

.006-.05

'Data from Eisenreich (1980); for southern Lake Michigan.

104 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

[Correlations not shown if majority of concentrations for an element were below the minimum reporting level (MRL). Correlations were done twice, first with 

MRL, and second with those values set to zero. If two coefficients are shown, the first represents the correlation where values below the MRL were set to the M

correlation where values below the MRL were set to zero. Elements with greater than 50 percent of observations below the MRL are not included in this table. 

H

oO

<o

Physical property 

or element

Aluminum, total

Arsenic, total

Arsenic, dissolved

Barium, total

Barium, dissolved

Boron, total

Boron, dissolved

Iron, total

Manganese, total

Manganese, dissolved

Phosphorus, total

Phosphorus, dissolved

Aluminum, 

total

1

.31

.30

_

.28

.29

..

.07

.06

.88

.57

.06

.24

.15

1 3 

E 3

0.31

.3

1

.64

.63

_

.07

-.15

-.13

.17

.16

.14

.13

.35

.33

.47

.45

._

.26

.24

.11

.09

Arsenic, dissolved

_

0.64

.63

1

-.19

.1

_ 2

.13

.39

.28

.38

.26

_

.16

.17

-.13

-.17

.3

.2

.18

.09

« *"

0.28

.29

_

.07

-.19

.10

1

.87

-.33

-.33

.3

.26

-.27

-.24

-.32

Barium, 

dissolved

-0.15

-.13

-.2

-.13

.87

1

-.31

-.30

-.29

._

-.25

-.26

-.35

-.36

* -o

All 40 sites

0.07 0.06 0.88

.17 .14 .35

16.07 .13 .33

.39 .38

.28 .26

-.33 -.33 .3

-.31 -.29

-.30

1 .99

.99 1

1

.69

.37 .37 .14

.81 .8 .23

.84 .83 .13

H If 

^ 4 ^"1 

0.57 0.06 

.47 -- 

.45 

.16 -.13 

.17 -.17 

.26 -.27 

-.25 

-.26

.37 

.37 

.69 .14 

1 .4 

.4 1 

.17 .32 

.4 
o Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

Major andT

2

g

m

<D

<D

1

5'

^

0)

5

!

3

<D

0)

a

005'

ST

<o

I

Physical property 

or element

Aluminum, 

total fl

Arsenic, dissolved lla * 

PQ

Barium, 

dissolved |i

Boron, dissolved n 1^

Manganese, 

dissolved

All 40 sites Continued

Strontium, total

Strontium, dissolved

Discharge

Specific conductance

pH

Temperature

Dissolved oxygen

Hardness

Alkalinity, total

Alkalinity, dissolved

Calcium, total

Calcium, dissolved

Magnesium, total

Magnesium, dissolved

-0.06

-.07

-.08

-.13

-.16

.32

-.34

-.22

-.67

-.44

-.1

-.17

-.19

-.25

__

-0.09

-.1

-.07

-.09

.08

.51

.5

-.42

-.40

-.41

-.39

--

-.54

-.52

-.4

-.39

-.43

-.41

-.15

-.12

-.18

-.16

0.29

.11

.29

-.28

 

.14

.13

._

.12

.58

 -

-.35

.06

-.33

.13

--

..

-.25

-.45

-.42

-.42

-.40

__

.09

._

.09

-0.05

-.06

-.07

-.06

-.05

-.19

.23

.13

.12

.24

-

.35

.17

.11

.38

.34

__

-0.19

.3

.05

.06

.25

.47

.76

.77

.35

.33

.54

.54

0.53

.53

-.37

.68

-.15

-.16

.1

-.22

.07

.37

..

.12

.14

._

__

0.54

.54

-.38

.69

-.14

.1

-.21

.09

.37

..

.14

.17

_

._

-0.14

-.15

.07

-.18

-.2

.3

-.38

-.26

-.62

-.51

-.1

-.17

-.28

-.33

__

-0.1

-.06

-.12

.31

-.33

-.19

-.51

-.46

-.1

-.09

-.15

-.13

-.18

-0.4

.39

-.37

-.15

-.23

.09

--

-.22

.22

.24

-.16

-.15
Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

1 .H 

Physical property jg J3 

or element "^

Sodium, total

Sodium, dissolved

Potassium, total 0.12 0.22

.2

Potassium, dissolved .15

.13

Chloride, dissolved

Solids, residue on -.18 -.24

evaporation at 1 80°C

Solids, total .73 .4

suspended .39

Solids, volatile .53 .44

.54 .43

Carbon, total organic . 1 .46 

.44

CP 

<D

<o

Arsenic, dissolved

0.26

.15

.26

.16

.3

.20

.31

.20

.15

 -

_

.18

.24

.29

.33

.37 

.15

 c 1

«8 *- 

03

-0.31

-.32

-.32

-.27

-.32

-.18

-.1

-.09

.31

.3

.18

_r *o *o 55 35 *o 

fl rti " * rti Q) d) 35 

|| |2 §| |3 || |! 

^^ ^* 

All 40 sites Continued

-0.26 0.84 0.84 -0.07 -- 0.4 

-.26 .85 .85 -.07 -- .39 

.84

-.32 .88 .87 .11 0.11 .37 

-.31 .89 .89 -- -- .37 

-.1 .74 .74 -.05 - .47 

-.09

.17 .65 .67 -.25 -.38 .18 

.66

.05 - - .74 .57 -- 

.06

.08 - -- .53 .5 -.08 

.09

-.08 - .32 -.16 

-.15
o Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

jF Physical property 

"5' or element

0)

a.

£

m

(D

3 Aluminum, total

(D

1

5' Arsenic, total

%5f

 ^ Arsenic, dissolved

I

| Barium, total

3

0)

o. Barium, dissolved

CO5'

-B Boron, total

«

<b Boron, dissolved

o

Cadmium, total

Chromium, total

Iron, total

Manganese, total

Manganese, dissolved

Nickel, total

Phosphorus, total

Aluminum, 

total

o"

|!

Arsenic, dissolved la

152 

tn

Barium, 

dissolved

o 2 

m

Boron, dissolved Cadmium, 

total

Chromium total c" <o

2*

Manganese, 

total

Manganese, 

dissolved 

3 

8 NAWQA sites

1

.36

.34

.07

.09

.43

.06

-.02

--

-.04

-

.09

.18

.15

.87

.54

-.18

.02

--

.14

0.36

.34

1

.64

.63

.08

.1

-.19

-.16

.07

--

.04

- 

.12

.2

.13

.39

.36

.55

.53

-.11

.09

.11

.16

.13

0.07

.09

.64

.63

1

-.18

-.11

_ 2

 .14

.38

.26

.36

.25

.1

.17

.02

--

_

.16

.17

-.16

-.20

.11

-

.29

.19

0.43

.08

.10

-.18

-.11

1

.81

.80

-.31

-.3

-.29

-.22

-.17

-.12

.43

.36

-.43

-.42

-.25

0.06

-.19

-.16

_ 2

-.14

.81

.80

1

-.23

-.22

-.19

-.34

-.36

-.23

.05

-

..

-.38

-.40

-.55

-.37

-0.02

.07

--

.38

-.31

-.23

1

1

.21

.11

-.16

-.29

.2

.3

.28

.83

.84

-0.04

..

.04

--

.36

.25

-.3

-.29

-.19

1

1

.18

.19

.11

-.19

-.31

-.32

.2

.28

.26

.82

0.09

.18

.12

.20

.1

.17

-.22

-.17

-.34

-.36

.21

.18

.19

1

.28

--

.04

.26

-.07

.23

.19

.13

.38

.28

.32

0.15

.13

.02

-.12

-.23

.11

.11

.28

--

1

.08

.09

.04

 

.21

.22

.5

.2

.21

0.87

.39

.36

.43

.05

-.16

-.19

.04

.26

.08

.09

1

.72

-.04

_

.01

0.54

.55

.53

.16

.17

.36

-.29

-.31

-.32

-.07

.23

.04

--

.72

 -

1

.07

.08

-.05

--

-.15

-.16

-0.18

-.11

-.16

-.20

-.43

-.38

 .4

.2

.2

.19

.13

.21

.22

-.04

--

.07

.08

1

.38

.37

.21

0

-

-

-

1
Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

Physical property 

or element

Aluminum, 

total

t[ o o> rf 

"c «? T5 

00 = -g

CO (A tO

l| aBarium, 

dissolved

og

o o 

m

il I 5 ° o c -g

2.8 I s

 0 0

E

|l 11

6

Manganese, 

total

Manganese, 

dissolved a 

1

8 NAWQA sites Continued

Phosphorus, dissolved

Strontium, total

Strontium, dissolved

Discharge

Specific conductance

pH

Temperature

Dissolved oxygen

Hardness

Alkalinity, total

Alkalinity, dissolved

Calcium, total

Calcium, dissolved

Magnesium, total

0.03

-.16

-.19

.07

-.25

-.18

.36

-.36

-.21

-.65

-.43

-.13

-.2

-.11

-0.02

.01

--

_

-.08 

-.09

-.15 

-.14

-.13 

-.14

.58 

.55

-.44 

-.42

-.45

-.42

.02

-.55 

-.52

-.48

-.45

-.5

-.47

-.09

0.18 -0.35 

.1 -.34

.29 .13

.3 .14

.3 .12

.31

-.26 -.33 

-.24 -.34

.15 -.21 

.11

-.02 .32

.59 .1 

.50

-.36 .13 

-.29

-.33 .3

-.28

-.01 .06

-.16 .32 

-.25

-.45 .19

-.42

-.42 .09

-.40

.03 .49 

.50

-0.34 

-.33

.3

.31

.32

.33

-.49 

-.50

.04

.48 

.49

-.05

.36

.64

.76

.77

.46

.41

.67

0.85

.4

.39

.4

-.34

.68

-.14

.16

-.14

.07

~

.35

.05

.06

-

.1

.08

0.84 0.26

.43 -.11

-.15

.42 -.14

.43 -.16

-.36 .29 

-.35 .26

.69 .03 

-.09

-.14 -.26 

-.35

.15 .05 

.12

-.12 -.28 

-.30

.12 -.31

-.37

.35 -.39

.1 -.39 

-.45

.09 -.22

-.32

.13 -.21

-.33

.11 -.36 

-.25

0.15 -0.1

-.17 -.34

-.18

-.2 -.36

.23 .13

-.05 -.37

07 0 ~~*.i. / *~.^

-.28

.14 .29

-.16 -.37 

-.17

-.26 -.19

-.78 -.6

-.15 -.48

-.17 -.05

-.16

-.17 -.12

-.16

-.3 -.2

-0.33 

-.33

-.28

-.29

-.30

.06

-.39

-.11 

-.10

.33

-.27

-.28

-.51

-.46

_>2

-.19

-.27

-.11 

-.12

0.32

-.34

-.35

.23 

.24

.16

-.41

-.27

-.14

_

-.31

-.19

.23

.27

-.43

0

-.

-.

-.

-.

-.

-.

-.

-.

 

-!

-.

-.

-.

-.

-.

-.

-.

-.

-.

-.
i Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

_ E"

JB Physical property § "55 

3 or element E 2

1 <

3

m

ID

3 Magnesium, dissolved -0.19

ID 

ft</>

5' Sodium, total -.11

^

?

-" Sodium, dissolved -.12

1

3 Potassium, total .04

2.

at

o_ Potassium, dissolved -.08

005"

F Chloride, dissolved -.09

<o

-j

£ Solids, residue on -.16

0 evaporation at 180 °C

Solids, total .54

suspended

Solids, volatile .43

.44

Carbon, total organic .12

.2 _

i o

Arsenic, dissolved

||m **

Barium, 

dissolved

P

Boron, dissolved Cadmium, 

total

Chromium total

II

Manganese, 

total

Manganese, 

dissolved

f 

8 NAWQA sites Continued

-0.13

-.11

-.03

--

-.04

--

.12

.09

.03

--

-.09

-.11

-.24

.41

.40

.5

.49

.46

.43

0.04

.08

.26

.15

.25

.15

.29

.19

.3

.19

.19

.10

-.01

 

.18

.24

.3

.33

.38

.35

0.43

-.3

-.31

-.23

-.3

-.21

-.09

.28

.29

.29

.1

.11

0.67

-.19

-.18

-.19

-.18

-.26

-.25

-.23

-.22

-.09

.18

.08

~

.1

-.12

0.09

.9

.89

.89

.91

.83

.65

-.05

~

.01

- 

-.05

0.12

.9

.9

.88

.89

.91

.83

.67

-.05

 -

.02

--

-.06

»

-0.37

-.28

.19

.18

.18

.24

.2

.14

.12

-.01

-.13

-.08

--

-.01

.10

.08

.09

-0.32

.11

.09

.10

.18

.14

.1

-.02

 

.25

.26

.21

.22

.11

-0.27

-.26

-.27

-.08

-.2

-.26

-.25

.47

.35

.36

.04

-0.18

-.33

-.34

-.36

-.2

.21

-.32

-.33

-.35

-.36

-.37

.46

.45

.41

.33

-0.41

.21

.2

.23

.21

.22

.15

.21

-.2

-.29

-.19

-0

-.
(/3 (/3 

c? S o o D D 

c' c' 3 3 

r+ p. 

c» on" 

p3 t/3 

O, <

8. -

o^ I

1

ff

00 OO i i OO 4^ Ln Lft 

OO H tO H OO J J 

00 -4 I

to

ONI

LoI

Ln in 4^ 

p^. 4^ to 

ON 4^ Lft 

so 

 P*

Lft ' k> so m ji. 

w

c' 3o

£.

oo

to

so

Lo' k _to

Lo 

ON

ON

ON1

Ij

Lo

-j

.1

Lo

Lft

.1

 *

> > > > 

 PI t-t 

C C W5 00 3 a ft ft 

355 a 

g' g P *' B- 3 o & 

,-> c» wa o & ~ S 

£L S 5* | 8. 

O)

4^- C> 9\ ' 

Lft so 00 

O i 

4^ i i O § *- O *- ! i Lo i 

8?a

3f o 

<* ^-j to Ln in ' 

JO OO SO UO Ki 

5*

{6£f , , , , aO

<*

MM ^ O 

a bo ! <i ! 

5? oo ON i i * p

bo 1 '-j Z«i Lo 

» -P* in 0\ J I ! Lo ^i Ipk 

OO -»1 Lft 

p

bo Lo ON 9\ i 

U> tO ' t 

P

4^. i Lo U> i 

to LO K> 

P J J J 

Lft ! 4i. £k to i 

H- U) K> ON P J J 

Lft ' 4^. ik ! oo oo <l 

 Q

?f

it9§

~O3 _ 

2.TJ 0 ^* ^

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Iron,

total

Manganese,

total

Manganese,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved 1 S

oto 

<p

C/5 C

3 3^oo

55

o'

52. 3O135 oCD" wo

cr

v>

CD

CD

Q.

D) 3o

3 

CO

 o

<no'

T>

3 

 o

CD

3- CD'

0)

Q.

CD

CD3

CD

5?

5"

52-

CD

5'

CDC o

"S

5' o55' 2

CD

03

03

v>3'

CO

00

 >J oo

2- 5' c

CD

Q.
Jofeft pue aoejj. siuauiaig u; 

' 'luauiipas pue 'etoig 06-8Z6L 

05iC3

on&C3B

E?

5*

£>

008

52.

p"g&1

CLJ

l/i

OsI J J 

LO (jA 

00 9s 

n S 

fid ^^ o CTQ 

r^* 3 3 e. c & 3 

VI . O ~* l < SJ ai i 

Os js- 

^o to 1 1 

to to 

-J Os J J 

Ln *> ! 

00

n

SLoc' 3**8Ei

Os1

to

Ln1 1 

'-^ j*. 

Os Ul 

1&.

Os

J

o\ I

LO

I

LO

I $ I Ln

I 

Ln

Os

dnity, 

ved

Hardn J

Os

J 

-J

I 

Ln I bs

Os 

Os

ed oxygen J

00

mp i i 

Os ^4 *- «>. ^o o oo --j 

j 

to I

Ln

I 

Ln

to Ln 9s 

2 % I 1 

{D l=rJ 

-3 o 

<8 o 

o. co

£ ?

o o1 ! Lo 

-j^ i Lo i i 

P ? ' k, 9 4^ i to 

yr os oo 

TO

1* P ' 

g. LO ^ 1

rt1 i : =

^ ^

ff5 P j T LO to 1 to *>. Oo9

9* l , O

Ln ' ^ ! Lo 

Ln ' 1 , P 

top

Os

TJ

sf

|S

T3 3 0 0 S^o

(D ** ^

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic, 

dissolved

Barium,

total

Barium,

dissolved

Iron,

total

Manganese, 

total

Manganese,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved 1 s

o- o

(O"

COc33

03OO

CD

S- ioo

o'

CD"

2^woa- w

CD3

CD

Q.

033o3

(O

o'

2. 1TJ

CD

3.

CD

(ft

03

OCD

CD

CD

(ft

5' ^

SCD

5'

CDC

TJ

TJ

CD=

5' o

(ft 5

CD

03

03

CO.

CO 

00!o2c

CD

Q.
n w w co n £ g. o 2. g. ^ 

2. g- ^p £ g- o P 3 § S < & &.§: E S- § I §§ S 1 o ? £§ -3 « 

o° 1 "' i i 

u> u> --J bv ON u> 

oo to U> <-» ! ! u> u> u> 

VO to Ov 

p .1 

! I ' fo ! ! 

-j

.' .' ... 

-P^- -^ <-» <~n t*» 4^- ' h ' i 00 \

u> ' b\ in in u> 

oo £ *> t*» Ov 

.' 

u> ' --J bv <?\ 

-fi. Ov «J 

p ! i i i U> 

to 1 1 u> u> in in In to 

U\ -P^ OO U) £t -J 1 i k. i ! ! ! i 

.1.1 .1 .1 

'-P^ 4^ U) U> U> k) 

+^ ^ -~J C/> 9\ OO 

.1 .1 \ .1 

U) -J <-» to U> -J 

S S 

p p^ 

vi En 

V> VI 

c' c' 

9 3 

"o & 

J? 60 

-e o 1 p

4^- U) 

^-rt *O O

4^- U) 

U) tO 

i i i i 

2?PB o * 9 K> K> U> > w -~j ve i S

5^3

i' o » !3 1 2aS1 : : i i , ^ 

S-' A£ p T u> to ? * 

5* ^1 P 

K> i 

Ov i i O

to to o

io K> ! 

Ov t*» 

0 1 

to to 

^n -~j P 1 

to to 

oo Os 

Physical property or element

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Iron,

total

Manganese, 

total

Manganese,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

Table 9.Summary

~^» Qoo

jsr 6" 3O1o'

5"

3^

5?oO"

u>

(D

(D

Q.

033

CQ

T3

o'

92.

 ao

3.

(5' w

a.

(D

(D3

(D

5' S

s.

(D

5" 5

(DC

T3

T3

(D

:s

5' OU)' 3

(D

GO

03wp

 L

CO

00IIoa3C

(D

Q.
Jofew pue COBJI siuauiao uj 'Jete/w 'lueunpas pue ' 06-8Z6L 

O O t%* ^ ^ ^0 ^"0 

| i" ? 1 1 I" 2 

1 | S 1 1 f f 

3 3 ~ § § 2 3 

O - " - 

 &* s IB i Jr* £ Cn * * o & M 

& * § EL § 

<* <* 

cx cx 

J

Lo 4^ 4^ vo bo Lo bo ON 

IO to W VO UO *-J *-J VO 

! !p>. Lo Lo io K> Lo Lo 

-o 4^ LO 4^ en to 

4^4^ 4^ e»> ON en --J ON ! enLft 4^ e»> 

00 h* CH tO 4^. 0000 K>4^ IO NO 

UJ i OJ *-J «-J tO 

.'....

O"\ L/i 

^O IO -P^ O> ON *J OJ 

, .' , .' , , .' .' 

i IO i LO i i W LO 

00 4^ > £>. 

1

! ! ! ! ! io ! LO

, . ! : ; i i 

00

. , 

! e*)Loe*)Lo ! 4^ k> Lo N> 

OO ON ~J K* 004^4^^^ 

. l 

' en4^4^-P^ ! N>toe»jLo 

5. ON vo O oo vo ON 00 

-^ 1 4^^.e*)Lo bo Lo bo ON 

oo ON -P^ ON LO ON O> ^-4 

_

Lo It) 4^ en bo ! *-~4 ON 

-4 10 VO O LO i J>. 

 ' ~ ' .' , 

i i U> i IO |O i ON o\ en 

.1 III 

i i to i l»i 4^. 4^ ! ! ! ON en -J vo 

..... . .1 J 

4^ K> Lo u) bo ^~4 ioio bo 

o\vooo4^.^- p eno\ 4^. 

LO |O IO |O ON ON i 00 

4^ 00 ON 00 -J 4^ 4^ 

J \ \ .1 _l \ 1 

! io io k> ON Lo I ON Lft 

ON ON -OJ 4^ Lft 

.' .' J J 1 I' 

to u) io '-J 4^. i ON Lft 

Lft -OJ ON LO Lft Lft 

> > cd Cd Cd Cd 

c £ § S 2 ° 

§ g | 1 g g 

g P' 3 - 3 - % "a 

3 a o & § »' 

- ° cf 5 S 

,» 83 P C« O 

S* s- "~ o 

1 I 8- 

n

cx

.'

Lo ON en '-j Lo ! ! 

-J i en 4^. LO 

. l 

Lo 4^ Lo ! ! 1 

* H- ^^ LO 

. , 

4^Lo ON^-4 ! e^^toLo 

,_.

Lo ^ ON i ! i 

LO Ln 00 

fc _ ! 

! ! ! ON ON 

io vo 

p _ > 

-J VO IO -J 

p . , "" 

4^ Jb« vo J 

, ; j 

' 4^ 4^ Lo 1 i io 

00 h- VO 00 

'f*. 'f*. ij) Lo i ! ! 

-j > en io 

.'

Lo ON en -j Lo ! ! 

^ ^^ ^ * 

Lo ^4 ON ^-4 i ! ! 

LO oo 00 ON 

1

io io ! io ! ! ! 4^. en ON 

II II II II II 

' ts>4^ enLft tolb toLn e*>Lft 

vovo OLO -U VO to ON MLft 

.' .' .' 

Lo Lft en ON Lo to io 

IO 4^. 10 -4 <-^ LO 00 

.'....

LO 4^ e*J Lft LO i i 

tO VO LO 4^ 

! ! i ^ Lft ON 

VO IO 

.'

to 1 ! --j Lft ON 

ON LO 4^. 

>c* 

3 5'

I

0

E

fc _ l 

p

Lo

-4

o

ON en 

i en 

o

^j

4^

^

Lo

LO

M4

I

1 ' 

SB5*

a ! 

S n

n3- 

§ 0 

» Lo 

g IO 

I*

^ 0 

& 4^ 4^ 

jf to w 

»

o

vo

vo

O

00

^

Lo

-4

^

! k 

0

bo

-4

O

ON 

vo

O

ON

IO

{L,

'-4

 o

sf

«s

(D 3"?

o (D S-o

(D ~ 

2i

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Chromium,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Selenium,

dissolved

Phosphorus,

total

Phosphorus, 

dissolved

Strontium,

total

Strontium,

dissolved

^&> 

cr 

o

(0

CO

c

3 

3

03

O

o

CD

to

o"

o

o

CD

o"

CD"

<n 

o

cr

CO

CD

i

Q.

B>

3

o

CO

~a

3-

o'

(0

SL

~o

S~o

CD

3. CD'

<n

03

Q.

CD 

CD

3

CD

<n

5"

0) 

CD-i

5"

CD

TJ

TJ

CD

5' 

O 

to'

33

CD-1

03

0)

CO p"

CO 

00

io

5'

c

CD

Q.
dissolve Magnesium, 

D.

J

in

00

!

!

.1

lo

1 -

to

K)

lo

J

jo

i

.1

in

00

.1

to

(^

1

1 'Q\

^

1

b\

to

bi

s

1n

22. c"

3

0

£

.1

x^

^^

i

i

i

to

OS

lo

00

"to

os

lo

J4^ 1 

1

1

UJ

1

lo 

to

!

'

1

in

~-j

1

in

^

00

dissolved Calcium, 

I

in

os

!

1 1 ~ 2> 

.1

os

lo

tO

!

1

' J 

-u in 

1 J 

lo U> 

so 00 

1

in

os

1

bs

00

!

£ SO 

I

in

UJ

1

in

00

-j

in

UJ

total Calcium, 

j

If^

-*J

i

i I 

os in 

<-n se 

1

lo

VO

to

00

1

1

1 1 

& b 

J

lo 

to

.1

1 "os

1

££

1 *4>-

00

1

in

00

in

VO

on on on n on o r >ffiOH

£ ? 3 » 1? ffi S 5- £ £ 

§ § § g- 2. ! s 1 I. 

I I I 1 f fail 

S: » o. 1 S3 cu 

I 1 1 ! 1 1' 

|ii I 

.110 1 J . J J .1 

! t>) ON *-J Lo ON 1^ 1^ ON ON *-J 

^^ to H-* (^ to -^ <^ to 

p . .1 

i ! to lo ! lo ! ! i i 

o\ to to 

10 1 1 1 1 1 1 1 

t>>lt^ ! 1 ! i^ w -jo\(/io\^lt^(/io\t»ji 

vo so seto K>u>inuj(>ivoc>iooh-^ 

P J , .' .' .' 

<~n in i i i uj i .fi. <^i -ti. i 

U) O <J\ UJ Ni 0\ 

i1 1 

-& SO OOtOJ^OOUJ UJ 

i1 1 

in i^t in in be ! j^to i < Cv 

t- j . . .' . . . . . 

*~n OJ CTN CTN oo i uj <*n i i LA 

in t») to <j\ i oo -~* 

110 1 1 1 1 1 

1 t IN^ bO (>^ 1 OJ (>} 1 1 |sj 1 ^ ^ <*/| xj 

^v ^-/i --J *^J *o ^N] 00 O ON k^ 

^ J J J J J . .' J .' .' 

K>tOK>> k>' i lo UJ itO ! *-4G\(>>U> 

i .1 .1 . .1 .1 . .1 .1 .1 

in j^. to so uj uj to 

0 J .1 .1 .1 .1 .1 .1 .1 

4^ ^ UJ 4^ i LA UJ CTs LA ON ON 

UJ4^se^J ON vo^-lvo^ 

^

! ! ! ! ! ! lo 4> 4^ ! ! 

-J 4^ in 

>- 1 

' ' !toK>lt ! It In I * 5>> ! 

4^ 00 4^ C\ h^ W 

0 .1 J J .1 .1 .1 

i (^ (^ ^^ (^ OJ tO Q\ (^ **J 

^/l ^^ ON ^/l VO ' H- 00 

.IP, ,.'.!. J J J 

Oi C/i oo --J oj C/i Oi L/I 

H- . 1 

i so b\ ^-J ji. ! lo l»i vo 

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, 0 H- .1 

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1-4

0. 1

5

1

3sa

reoso

n

F

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ff

06

I

O

3*

i

Physical property or element

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Chromium,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Selenium,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

Table 9.Summa

*<

o 

o

CD

of

5'

8CD

o'

CD'

5T

o

cr

U)

m

a.

o>

o

fO

^3

'w

o"

E.

T3

O o

CD"

U)

o>

fS

CDCD"

3

CD

to 

5"

i.

5"

1 3

CD

c

T3 

T3

CD

=

3'

oCfl"

JJ<"

03

0>

CO p"

_i.

CO

00

CO

oJ3^

5'

c

CD

Q.
Jofeft pue eoejj. s}ueuie|3 u; ' 'lueunpas pue ' 1 06-8Z6 

n

o 

o 

o

to 

n'

Lft 1 1

Lo

*-J ^ 

^

b\

1

to

!

U> W 

ON E 

u> w 

ON W 

OJ

b\

C/l

'

.1 J 

Lft

1 1

Lft

!

1

N>

o o o o cr o^o 

oooooon^o^owc/D

o 

& B: » » 5" z- < x- xi i g. g. | !& & & 

p p c c S- _, ^ . < 

s & 3 3 £ 32 ! | 

» s s o. s 5 5'& !r g. 

^ | 1 i a ^S 1 ^ 

S S. < 2 » 'o 

o. < JP p "- 2 

fl) 0. 00 3 

°- «=> & 

n o. 

P .' , .' J 

-P^ Cft 

K-K-OO

4^ i ON ON ON ON ~J 

O^O-J^-J 

P .' ...,.' 

to to ! I to i 4^. Lo W 

ON 4^ vO OJ t/i JU 

0 1 1 

! ! o)Ip^(/iLft ' 4^ ju Lt ju Lt cn 

tn^o *\^- t-^ox oc^- \o &\ 

P .' .' 

' ' o\ *pk Lo 4> Lo Ipk ^ 

to u) oo oo to W 

5* 0 II 

S b\ b\ i to Lft to 4^. 4^. 

>g Lft OO OJ VO Cft H5*

* P . . . . , .1 .1 J 

» bo ^ Lo 4> <i i Lo k>N> 

J^t/i-JOJ"' «JO\tO 

a

n P . . . , J.i 

-JCft^OOOOg" i K>OJ 

g. ^] 4> N) U> 4^. O\ 

CO

a

%

~~ , , P , , , .' J , 

iB i ilu> i i(j)U) < {jt 

^ 00 N) O K> 

S*

^ i 1 I I I 

Y i ! K> to K> ! to K> '$> In !p». ^'4^. 

1 -a oo Cft Lfto^oooo to *k 

n

0

P»' J . , .' .' 

4^.c Lft 4^. ! b\ b\ b\ ^jb\ 

O\Q, tO OOOO\(-ftO\ 

P .' .' 

i i C/i O^ tO *^-J C/i L/i C/l 

**j Os oo » » ^ (/I 

O 1 

\ : ; i bio i : to 

^ O ^ 

0§ J § J J J J J 

4^ i t>J i ON 4U ON 4U i to 4U i i 

|O OO '9\IO 1 O ON O 

10 _ II 

Cft Cft 4^ i O\ O\ O\ 9\O\ 

OJ 4^ 4^ OJ (^i Cft 9\ 

.10 . . J .1 

4^4^~-J4^Lo4^Lo4^

vo o\ H- Cft > O\ Cft 

0 1 1 

<i <i i ! bo ON 4> 4> 

0 . Jll 

<i <i ! ! bo b\ 4^. Lft In 

ON to \O h^ 

Physical property or element

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Barium,

total

Barium, 

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Chromium,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Selenium,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

i 

9. of able Summary 

o

o

3L

o' 2*

o

o

CD

o'

CD'

CO

o

CT

CO

CD

I

CL

1

O 

CO

-a

IT

COo'

D>

TJ

3

TJ 

CD

CO

ftt

0.

CD

CD

3

CD

CO

5'

1CD i

5'

CD

C 

TJ

TJ

CD

5'

o co'

3

CD

03

CO p'

CO

00

rCO

1

o

o

5'

c

CD

0.
n n n t? r 

8. g- 3 § 8 

§ c 1 P. 1 * -T1 2. o Si?

3 | g- £ 1 

a '^ S" ~ 

55' g. "^ 

<L £ <*

a

! Lo la Lo la vo Lj 

LO ' 1 O\ SO -J 4i. 

Lo ! ! ! ! 

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H* -J LA 

' : : : k»kj 

-J os 

...'.'

Lo k> Lo ik ! 4^- la 4k ik 

to so 4^ t i vo so LO in 

.1 } 1 Ji } 

Lo la ! Lo ik ! la ! 

11111

11111

LA In ! Lo la Lo Lo la 

' i 4^- in oo oo a 

H1 1 1 1 

fc __ t 

> 4^ la Lo la Lo la 

in 4^> K) LA ta 

. l 

i 4^ la Lo ik LA 

in VO ' I LA 

i LO ta LO 4^ bo 

4^ K> vo ' 1 

H-

! Lo la LA bo 

LA ta LA 

' LA in Lo la 4^. LA 

LA OS LA 9\ OO -J 

J

to i {^} (^ i ' I 

OO K> 

> 4^> In Lo ! ! K> Lo ik 

c\ o\ LO so LO ta 

11111

1 1 1 1 1 1 1 1 1 1 

1 1 1 1 1 

1 1 

I i to Lo ! oo oo 

' ' 1 

i i to 4i- to 

OO LO OO 

J> i»I> i> W W Gd OW 

53c-£- 53 85 | R S g. 

3 ">3 o jr = o HO 

3. 23. 2 3 3 s B§ 

3 003 P P "« o =' 

-CC 3CL?T 

3 3 o & o & g 5T £ 

* SJ* ^ & U5 oO 

S-^S-^S <* g 

£ S ^ <" ft 1 

o o o o. 

5- ex c^ 

CT

a.

! LA ! LA ik ! ! ! Lo la 

to LO 4^. LO K) 

H1 1 1 1 1 1 1 1 

P ~ . . .' 

LA ! LA In ! la to ! Lo to I 

to LO K> O 00 O\ VO 

O ^ H- 

! ! LA in ! ! "-J ^a "-J ! 

LO Ki -J 00 4^ 

° . *" 

LA ik ! ! la ! LA in ! ! ! 

LO 4^. O LA K) 

1 H- II 

' ' kj ' LA In i ! 4i- ik 

g K»LA 4^tO 

n , , P ... , ~ 

5? i i LO ~J ^4 i i vo i 

5 O\ -J 00 VO 

og" H- 1 

'5* ! to '-j ! i vo to 

» vo 4i- vo <?v 

5 0 , , J J .1 

? LO w ' ! ! ! fe it ! ^ 

£

i , i , , j j j j , ... 

' «! Li ' i itaLOKJLO InLAi 

» J3 to so 4*. ta H* 

ffi.

a. 

* P . . .' , 

 - Lo la I 4x ik 1 Lo ik ! I > \ 

! LO ' h- -» 4^ > l 

sr P . , , .' .' ... 

^ LO ta it i i LO 4^ i i LO ta 

o o\ so > o 4^- in 

P , . , ,.',.. 

vo ' LA ! 4^ La ! La ! ! Lo 

-J -J vo so » i oo 

P

~J LAI !4^4^K)to i taLo! 

4^ inLoe\-^jLA oo ~a 

P

OO OO tO ' h- 

«=> .' 

LO ^ 

P

! 1 Lo ik 1 to la i ! ! ! 

N) C\ 9\ 

0

-^ , 

, i i , i ii 

0\

, P ... .' , . . I 

i 4^-1 o\ g\ i LO i oo oo i 

O\ -J O\ LA LO 

i ' 1 

, : ! Lo b\ g\ Lo la I bo bo ! 

g; to oooi-»to 4^- 4^- 

i , , ,..'.. 

',.-. ii O\ 9\ LO i i VO OO i 

Q; i O H- OO 

^ 1 1 v ' ' b\ to ! ! bo bo Lo 

5 vo vo oo o\ 

of

g (0 

"°

(D 3 

3 | 

^ "* 

h.

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Cadmium,

dissolved

Chromium,

total

Copper,

total

Iron,

total

Lead,

total

Manganese,

total

Manganese,

dissolved

Nickel,

total

Nickel,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved
It Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Riv

s

fl> "o"

fl>

Q.

3

g

m

<D

!

sr5'

L?

5~SP

2.

3

<D

3

Q.

CD

f

(O

£0

Physical property 

or element

Manganese, total

Manganese, dissolved

Nickel, total

Nickel, dissolved

Phosphorus, total

Phosphorus, dissolved

Strontium, total

Strontium, dissolved

Discharge

Specific conductance

pH

Temperature

Dissolved oxygen

Hardness

1 11 o of

=5 =| g 1 § | 

E o E 8 So SI w

3 3 .« £ £ .W

0.48 -- 0.28

-- -0.43

-.44

.3

.42

i/; .Zo

"

.46 .67

.66

-.26 -- .32 .62

.61

-.36 -- - .61

.60

-.43 -- -- .6

.31 -- -- -.66

-.55 -- -.28

.. -Q.31 --

.38 -- .52 .61

-.51 -- -.45 -.31

-.64 -- -.59

||m **

0.62

.61

.26

.36

-.38

-.3

-.31

--

-.29

.39

.28

-.33

-.30

-.29

~

.34

.45

-.34

-.32

_

 .T? "9 e" c^TJp 

C V " - ft) S C $ = kT

m =5 '-DO o '-5 Q °

Des Plaines River at Riverside, 111. (site 40) Continued

0.55 0.35 0.48 0.57

.56 .36

- -0.28 .3

.32

.46 .33 -- .33

.56 -- .29 .43

0.3 0.85 0.83 --

--

84 84

.9 .88 -- -- -- -.28 -.38 --

.89 .88 -0.36 - -- -.28 -.43 -.28

-.88 -.89 .27 -- .26 .26 .29 --

.27

.26 -- -- -.36 -- -- -.36 -.63 -.71

.31

.34 .38 -- -- - -- .4 .68

-.32 -.53 -.7

-.34

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.49 -.38 -.39

of «T 

I |* 

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1 0.31 

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-.33 -.35 

.49 -.38 

-.37 

_.41 ..

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on on on n 

K « K K ! 

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t/5 IB r» 2. O 

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-£> LO LO 

io ! ! ! ! ! fe ! b '* fe 1 1 1 1 ! ! to ! ON

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dissolved Potassium, dissolved Chloride, i i 

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Physical property or element

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Cadmium,

dissolved

Chromium,

total

Copper, 

total

Iron,

total

Lead,

total

Manganese,

total

Manganese,

dissolved

Nickel,

total

Nickel,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

Table 9.Summar

«< 

o^

o o

CD

o' 21oo

CD

CD' If

OToO"

v>

CD

Q.

0)

3 o

{Q

-Q

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o'

03_

-oo

CD

CD"

(0D

CD

CD

CD

?. $

0)

CD^

5"

CDC o5=

3'

§ 2®

CD 

0)

CO p'

CO

00

^^

CO

^5oo

5'

CD 

Q.
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1 g B 

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O OS OS 

£L 8 8 

'r» ^V 

2-

CL

bo to ! 

-j

i i i 

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-j

| 1 

i tO tO 

i i 

i to Lo 

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,

Lo U) i 00 to ON 

-£ vo O Ln vo 

& ' 1 

$ &S ££ 

l _l

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total

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Chromium,

total

Copper,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Nickel,

total

Nickel,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

CT 

A

to

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c 

3 

3

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S & | £ 1 S £ - 

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re

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p i 

p

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OJ

p

i Lo lh> 

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of

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Aluminum,

total

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Chromium,

total

Copper,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Nickel,

total

Nickel,

dissolved

Phosphorus,

total

Phosphorus,

dissolved

Strontium, 

total

Strontium,

dissolved

Table 9.

CO

c

3

3

o>

>5

a

o 

o

S

SI o"

D 

O

O

=* o'

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w

oO"

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3-

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1

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5'

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§ & g' !'§* £* £ * 

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cp 3-5 

£ o <D 

3 £ § 

q 

5 3 

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5 total 

5' Arsenic, 

= total 

o

(D

3- Arsenic, 

CD' dissolved 

3.

CO . _ 

o Barium, 

% total 

(D

^

CD Barium, 

p> dissolved 

3

o _ 

^ Boron, 

-o total 

CO _ 

5' Boron, 

Q) .... 

dissolved 

 o

3

"§ Cadmium, 

3-. total 

CD

CO

§ Chromium, 

J total 

CD

3 Copper, 

S total 

CO

| Iron, 

0> total 

CD

5' Manganese, 

5 total 

CD

C

^§ Manganese, 

5 dissolved 

o Nickel, 

' 5 total 

5

| Nickel, 

CD dissolved 

CO

- Phosphorus, 

co total 

00

r

<£> Phosphorus, 

| dissolved 

0

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i total 

CD

Q.

Strontium,

dissolved
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Aluminum,

total

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Copper,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Phosphorus, 

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

u- ^

9 

CO

CO

C

3

SO

o

o

CD

6' S.

D

O 

O

o|

D 

CO

o

cr

CO

(D

1

SO

3

o

D

CO 

TJ

f

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T3 

(D

a.

CO

D

Q.

(D

(D

3

(D

CO

5'

$

S"

5'

(D

C 

T3

T3

CD

5'

co' O

CD

OD

CO p'

CO 

00

t

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D^

5'

c

(D 

Q.
12 Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Ri

Major and1

i

m

0)

3

sr5' 

S

0)

0 

I

(D

j*

0)

3

Q. 

OJ o'

5f

w

?

(0

o

Physical property 

or element

Aluminum, 

total

0 ti «

*c To 'c 

w 2 w w 

<C <C *~

.3 $ * -| gs

to ** (D . CQ **

Boron, dissolved

hT

a. 2

11

0) 0) T,

w w Trf

0) _ 0) $

c n c .2

O) O O) W

c c .2

i 1=5

Du Page River at Shorewood, 111. (site 69) Continued

Phosphorus, dissolved

Strontium, total

Strontium, dissolved

Discharge

Specific conductance

P

Temperature

Dissolved oxygen

Hardness

Alkalinity, total

Alkalinity, dissolved

Calcium, total

Calcium dissolved

-0.61

-.68

-.69

.69

-.73

-.49

.24

-.55

-.77

-.86

-.73

-.68

-.74

0.43 

.27

.47 

.40

.47 

.40

-.57 

-.46

.48 

.45

.3

.26

0.64 .61 

.61 .55

-.31 

-.24

-.31 

-.23

--

.56

-.37 

-.29

-.39 

-.31

-0.6 .. 0.71

-.61 .. .89

-.62 _ .9

.67 .. -.85

-.63 .. .7

-.31 .. .46

.25 

.26

-.52

-.52 .28 .64

-

-.52 .. .78

-.43 .3 .55

-.53 .29 .58

0.7

.91

.92

-.85

.69

.47

.26 

.27

--

.64

--

.77

.55

.58

-0.36 

-.32

-.36 

-.40

-.38 

-.42

.44 

.45

-.38 

-.45

-.33

-.39

-.32 

-.35

-.49 

-.50

--

--

-.42 

-.45

-.49 

-.50

-0.61

-.75

-.76

.72

-.75

-.51

.23

-.61

-.78

-.9

-.72

-.7

-.77

-0.68

-.69

7 / 

.7

-.68

-.39

.36

-.57

-.72

-.86

-.81 -0.61

-.66

-.74
Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois R

s1

oW

(O

Physical property 

or element

Magnesium, total

Magnesium, dissolved

Sodium, total

Sodium, dissolved

Potassium, total

Potassium, dissolved

Chloride, dissolved

Solids, residue on

evaporation at

180°C

Solids, total suspended

Solids, volatile

Carbon, total organic

Aluminum total

-0.75

-.78

-.69

-.7

-.49

-.64

-.77

-.77

.38

.43 

.44

.24

o

'E Q

I 2

-0.27

-.27 

-.21

--

--

.21

--

--

_

.33 

.30

.55 

.54

.62 

.59

Arsenic, dissolved

--

.22

.37 

.36

.37 

.36

.55 

.47

.52 

.45

.42

>i1

.43

.47

.36

.33 

.44

.34 

.41

-"§ « -"§ 

 i 1 -i o 2 1 2 1

TJ B

Du Page River at Shorewood, 111.

-0.51 0.25 0.68 0.68

-.56 .26 .69 .69

-.62 .. .81 .82

-.65 .. .82 .83

-.46 .. .9 .89

-.64 .. .91 .93

-.75 .. .68 .7

-.77 .. .73 .75

--

.32

-.47

,.

<5 -_ 0>_ ® 8 

Q. 03 c jo Cjo mo 

|S 22 0,0 gj 

0 II*

(site 69) Continued

-0.46 -0.76 -0.68 

-.47

-.52 -.8 -.73

-.35 -.76 -.68 0.21 

-.39

-.39 -.76 -.7 

-.41

-.55 -.49 

-.24

-.34 -.7 -.66 

-.39

-.46 -.83 -.76 .28

-.48

-.45 -.82 -.78 .21

-.49

.34 .37

.32 .41 .54 .38 

.31 .42 .55 .37

.37 -- .24 .27 

.38
^ Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Ri

JS o'

u Physical property 

a. or element

!

m

o> Aluminum, total

jf

(0

3 Arsenic, total

15

-1 Arsenic, dissolved

iCD Barium, total

2

u

3

o- Barium, dissolved

00

o

S

1* Boron, total

?

o Boron, dissolved

Cadmium, total

Cadmium, dissolved

Chromium, total

Copper, total

Iron, total

Manganese, total

1 "

IS 13 

£0 go

|1 |- 

? | | §

t£ $ - > $ E

l| j! || |l

00 =5 'Bo

 2 > I ro E o E § 

 § w o o

CO rO TJ o

£3

%2

£ s

2 o

Manganese, 

total

u-o

c 5 T

8,8 |o

Illinois River at Marseilles, 111. (site 76)

1 0.36

.35

.36 1

.35

.54

.63

.51

-.28

-.26

-.41

-.41

.24

.23

-.27

--

.32

.27 .23

.26 .21

.88 .31

.30

.66

0.51

0.54

.63

1 -.46

-.41

-.46 1

-.41

-.45 .79

-.44

.55 -.76

.47

.54 -.77

.46

__

.39

-.24

- 

_.

.25

.29

.53

-.26 .57

-- -0.41 -0.41

0.23

-0.28 - - .24

-.26

-.45 .55 .54

-.44 .47 .46 .39

.79 -.76 -.77

1 -.56 -.52 -.28

--

-.56 1 .98

-.52 .98 1

-.28 - - 1

--

.23 - .6

.27 .27 .71

.33

.51

-.5 -.51

.30

.38 -.44 -.44

.28

-0.27 ~

-

0.32

_.

-.24

..

_.

.23

.27

..

.27

.6

.71

1

-.26

1

-.26

.3

.26

-.29 -

--

-.26 --

0.27

.26

.23

.21

.25

.29

_.

.33

.51

..

.26

.3

1

.24

.22

.25

.23

0.88

.31

.30

_

.53

-.5

-.51

..

.30

-.29

--

__

.24

.22

1

.76

0.66

-.26

.57

.38

-.44

-.44

_.

.28

-.26

 

.25

.23

.76

1

-- -0.2

--

-0.52

.50

-.48

-.45 .2

-.2

..

.25

.2

.2

.2

.2

__

.4

.4

.3

.3

_

.23

.24
Table 9. Summary of correlation coefficients observed among physical properties and elements in water in the upper Illinois Ri

Physical property 

or element

j! J! $2 Is 2

<! »

- g -

II M

1.2 «§ 2

TJ " TJ C * *" TJ 

 $ E £ « 1 l-' 2 |2 $ - 

II la II la &a §a gs ll &s 

o§ £Q £M o £ § P 2 3 0)0 S) oo uo 

to .2 ra S.2 £ o ~ g §-2 z 

° 55 

Illinois River at Marseilles, 111. (site 76) Continued

Manganese, dissolved

Nickel, total

Nickel, dissolved

Phosphorus, total

Phosphorus, dissolved

Strontium, total

Strontium, dissolved

Discharge

Specific conductance

PH 

Temperature

Dissolved oxygen

g. Hardness

<D

<o

-- -0.52

-.50

-0.23

--

-.35

-.31

.43

.42

-.4

-.5 -.39

-.38

-.59 -.44

-.43

.54

-.29 -.6

-.24 -.45

.61 

.60

-.32 -.65

-.64

-.64 

-.63

-0.48

-.45

- -0.21

.27

.27 -.31

.34 -.29

.37 -.56

.39

.37 -.81

.34

-.23

-- -.32

-.43 .72

-.36

-.54 --

-.60

-.25

.64 

.62

-.62

-.64

-.57 .47 

-.65

0.25

0.27

.26

.44

.43

-.72 .59

-.7 .78

.52

.5

.47 -.69

.31

.23

.65 -.37

0.23 1 -- 

.24

0.27 -- -- 0.46 0.38 -- -- -- 1 

.25 .45 .39 

.48 -- -- -- -- -0.38 -- -- .6 

.46 -.33 .5

.53 0.23 - - .22 -- -- -.26 .2

.28 .24 .2

.75 -- -- - -- -.49 -.49 - -- 

.49 -- -- " ~ -.52 -.26 .28 .2

.2

.5 - -- -- -.23 -.63 -.34 .35 .2

-.25 -- .2

-.65 -- -0.24 -- -- .63 .67 .31 -- 

-.24 -.35 -.24 - .56 -- 

-.36

22

-.26

-.22 -- -- .64 -- 

-.32 -.29 - - -.25 -- - .51 -.2

-.24
931. Jofe^ pue aoeji siuauiao ui 'J91B/W 'B)O)g 06-8Z6L 

total Carbon, org

to

o'

'fv

to

1

1

£

I

I

1

!

i

1

1

Lo

 ^

to

SO

1

1

!

!

1

'

total Solids, suspended volatile Solids, 

^ Lft 

Lft

u> w Lft en 

Lfi t± Lft £k 

i tO lfc> 

Os 9s 

i ! 

to ! oo

1

Lo ! Os

J

Lo ! 

to

! ! 

J

Lo I ! 

""^

! ! 

! 1 

^ LA 

to to 

bs ji. 

Os 10 

1 1 

fcfK

i i 

j ! 

1

.1 1 

Lo to 

Lfi OO 

1 1 

'.p*. Lo 

> to 

oo '-o >-o n oo 

a s s k s. « 

r g s s & £ 

§ 2. 2. g: " »§ 

P C C g* O-i 

& 3 3 - a 8. i 

1 o & Si' I'i* 

1 E 1 i- &i p. ^ n> *j H 

ft O. OO 

O. O 

ri

.' J .' J J 

j^ to ipi. Lo to 

Os LO LO ~~) -P*. 

II 1 1 1 1 

Lo oi Lo ! Lft In bs 9s 

oo -a so oo os en 

J J J J 

! Lo to Lo w " £ in Lft bs 

-J OO 1 OOs OS HJ J J , 

'.p*. Lft ^~j i i 

to so .pi. 

1 1 

! Lft Lft ! j^. 

~-J ~-J so 

j^. LA --J to ' 

~~1 Lfi -- U) 

ji. Lft ^ to ' 

SO Os U) ~J 

\ J \ 

' ' ! ' K> £> JU 

en to in 

!!!! ! 

1 1 

' 1 ! ! to to 

Lfi 4k 

J J 

! ! ! t Lo Oi 

tO H* 

1 III 

*^ ! Ji. Lo to 

Os 4^ Os Os 

J

ij ! ! ^ij ^ 

! Lo bi Lo to ! ' 

oo en to so 

4± lit to ! '-t- lh» to > > OO U) U) \O 4*. 

1

to bs '-f». I '4^. 

l>) tj) p^ SO 

OO S -fi 

bs i Lo bs j^. 

--J ' ^. bs Lft 

to so -l^- 

Magnesium, dissolved 

total Sodium, 

^

! ' li. 

.1 \ .1 

bs bs Lo 

o so 

1 1 

Lft bs ! 

SO -J 

J

'4^. Lo 

SO SO 

bs ! ->j

1

Lo j^. 

^J ^j 

J

Lo j^ 

so

1 J 

Lo tjt I 

so e*^ 

I

to ! ! 

to

P ' 

to 1 

J

Lo I 

to

^

! Lo 

Os

' ! 

SO OO 

o

^ w 

1

bs to 

i l^ 

1 

Lo ^ 

-l^ oo 

'-Pi. bs 

h- OO 

^ bs 

SO

i

c' 

3

o

^

!

1 1 

Lft en 

os en 

\ \ 

bs <t 

Os K> 

bs

lj

i«^

1 '[^

to

J

Lo

oo

1

to ! 

^J

o

io 

to

1

'

i

oo

$

1

1

.1

Lft

~J

\

Lfi

Lo

dissolv Calcium, 

O.

!

1 1 

bs bs 

Lfi .U 

1 J 

Lft bs 

Os *> 

Os

bs

^^

1 '[^

1

Lo

1

Lo

U)

i

i

1 J 

Lo l*> 

j

'

Lft

1

I

bs

to

\ 

Lo

Lfi

Lo

Lo

£ P 

£J O 

I 1' 

*< % 

a 8- 

& EL 

°

^

a.

i i 

i I I 

<i bs bs 

j^ u> to 

i> j j 

> en os 9\ 

9s to v« 

O

! Lft 

0

' bs 

Os

5 , P 

5' I '-P^ 

SB*

5 i 

» ! Lo 

1 Lfi 

£

i ^ i 

S ! to to 

g -P^ K» 

g 

J*

E- ! ! ~

ce

ff

-j i i 

-2s

? i I 

2. bs bs ' >2* Lft ^^ 

3

e

g.

! ! 

o

! to 

o

! Lft 

to

^ j 

3*£

' ' 

P .' 

Lft Lft 

SO

, o 

' Lo 

oo

p

Lft Lo 

U) Os 

O

Lft Lo 

oo -P*. 

Physical prop or element

9 ~ 

3

Aluminum,

total

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Cadmium,

dissolved

Chromium,

total

Copper,

total

Iron,

total

Manganese,

total

Manganese,

dissolved

Nickel,

total

Nickel,

dissolved

Phosphorus,

total

Phosphorus, 

dissolved

Strontium,

total

Strontium,

dissolved

1 s

cr 

o

CO

c

3

3

0

o 

o-t 

-^

5T

6'

3

o 

o

CD

=fc o'

o>'

5f

0

(0

CD

i

Q.

05

3

0

CQ

-Q

3-

1

i.

-Q

3

a

a. 5'

~j

Q.

(D.

I 

CD

«

5'

3"1

-<i

5"

c

T3 

T3

CD

_

055'

CD

0?

(0_5'

CO

~9

CO

I

o

5'

CD

Q.
621.

c/3c/ihohogsrwwww>;>

' 0 ' 0

g3oos§2.2.§ES23 22^oo.3p3o3'e'

5 si t/> 8L nj; i i' -. i o n Bt i

1 o 2- <T o g- o. g- 55 5- < o g § B- & 8 

o n o- £ £L t» 2. 

o. o. o < 

£ & 

CL

1 _ , . , 1 1 

bx LnlnLn to Lo Lo bo ^-j bx k> N> Lo Lo 

LO ON in H- H- Ln u> vo vo -& Loi*ito LO 

1 1 1 1 1 oooo enLn to inLn inLn -J ~j -J -J ~j i*iu> 4s. £t .£» 4t 

Ln ** to W vo Ln 9\ £tU> 4s. W oo >-- O 4s. OO inox K>u> 

~ . . .' J . . . . . . . . .' J .' J 

oobo l»)4s. k> k> InLn inLn o\'a\ bx 9\ b\ 9\ Lo (*> LjLo Lo k) 

«kLn 4^»"OO OOLO^>Ol*iLOOtOt>>LOI-'LoentOJik 

Hl»i4s.inLn 4> 4s. 4s. 4s. 4> Ln 'IwLo ! 

l»Jto OO 4*. -J Ox -J 4s. to 9\4s. 

.' .' J ~ J .' J 

to to k) i^. ! ! Lo 4s. to ! Lo 4s. 

^ _ ^ 

4s.enLninLn i (o Lo Lo '*>. ikito ! 

LH ON *k -J inLotooxvOLn 

. , 

4s.inLninLn ! \o *4s.LoLo ! ! ! 

oxintojikLo Ln -j ' i 

J . ~ . . J J 

-»J «4 ON 9s 4>> Lo Lo Lo bo ^j 4s.l»iLo Ln 

Jh^OJl»)4s. OO VO ~~1 VO OO OOJSkOJ ' i 

.' . . ~ . .' .' 

^-J Ox 9s 4> 4s. Lo Lo bo ^-J to i>> 4s. 4s. 

oo 4xt>>u> Ln Ox vo LO oo~jox oo 

.' . . . ^ J J 

Ln9sOx~J--J to 4s. 4s* ~J ~-J 4s.Jik4s. 4s. 

tOOtOOn- i to oo LO -J~JOx -J 

^^

Lol^Lo Lo U) ! k) k> ! ^4s.t>>fol*iLo 1 ! 

LOO04S. 9\4s. inLO U> ** ON -4 O\ -4 

J J .1 J .1 .1 1 ~ 

4s. £t Lo U) ! Lo ! ! 4s. 4s. 4s. ! \O 

jsk^oenox -j -~JOOOQ 4s. 

1 J 1 J 1 1 | H4s. £k Lo W ' 4s. i ! Ln 4s. 4s. ! VO 

OOLOt>>LO U> t OO -J 4s. 

total Aluminum, 

-_i

o

bx

LO

O

Ln in 

ox in 

o

Ln

c?

X

9 i 

q k> 

to ^ 

r*

^

1

A O 

| Lo 

Hr 

£.

* O 

-5 "w 

o

bo 

vo

p

^0

p

o

k) ts> 

to u» 

o 

Lo

LO

cL,

Lo

LO

pro Physical or elemei

^ j» 

2

 <

Aluminum,

total

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Iron,

total

Manganese,

total

Phosphorus,

total

Phosphorus,

dissolved

Strontium, 

total

Strontium,

dissolved

or

(D

to

CO

c 

3

3

w

^

o

o

cB

»

i

o

o

o'

CD'

5f

o

cr

w

CD

CD

Q.

0>

3

o

(Q 

|-

o' W

9L

|

CD

a. CD'

w

Q.

CD

CD

3

CD

5T

5'

2-

CD

5'

CD

C

^^ 

^^

CD

5"

^

ow"

5

CD n

03

(03"

CO 

00

rCO

 Cont 0 

3

C

CD

Q.
O C/3 t/3 W O 

a* p. CT p p £5 

5" £ < |: S § 

51 ^ ^5 ^ 3 

* rf ^ O S r^- 

£! §:& 1 1 W & O r^ & s § D S sr o 

Si _ J» CB S» 

< 2 -^ "o cro o a K o P 

ex oo 5 2. 

q 8- " n ex 

^ ! ia 2 5i2 1 P .' 

OO -J U) h- Ji. 0 1 ! l>-> l»j lf\ In 9\ON to K> 

OO -J OJ h- (/ION OO OJ 

P

k> ! ji. ii. bi ! 

o» ON tn vo 

oX

50 ^ P 

5o 00 4^ 00 ij 

s>

,.^^

 85 o 

S. u> ! ! u> ! p N> O» 

>3

r ^M 0 

00 i t 

.'P

t>) ON ON ON {/\ i 

o^ o^ O (| 00 vO 

JO

^>> ON -*J -*J i 

U> -J -J h ^ ! u> u» In "-^. i^ ! 

^D ^^ Cj^ t^rN «*J 

^5 ! io t ! ! 

h-^

.0 J J £ ^ 00^0 p . J 

ON -J 4^. 

 o

of

ical property 

r element

Aluminum,

total

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron,

dissolved

Iron,

total

Manganese,

total

Phosphorus,

total

Phosphorus,

dissolved

Strontium,

total

Strontium,

dissolved

_^

cr

CD

(O

of Summary o03

fB.

o' D08=* o'

CD'

5To

CT

CO 

CDi

Q.

SO3o

(Q 

TJ

COo"

8L

T33

TJ

CD

a. CD'

CO

SO

a.

CD

CD3

CD

5T

5"1CD t

5'

^^

IT

CDC

TJ"8

 i

5' oco' 5®

GO

SO

CO p'

CO

00rCOIo

5" c

CD

Q.
Jofe^ pue aoejj. s)uauia|3 u; 'JajeM 'luaunpas pue 

to Phosphorus, di Phosphorus, 

5* v> 

£ 2 

O

I D.

00

' 1 

bvbv ! ON to 

b\ In ! 

o

! lo Itt 

to u» 

' £ *> 

In In ! k i 

4^ ! 

00

1 1 

4^ ! 

1 J 

ON to to 

-&. 00 -J 

^ 1

'

! lo u» 

t*> O 

' ' 

3

era

D 

0

P_

00

to

1

-J -J 

In In 

o\ to 

lo

Ut

'

1

!

: to 

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bo

~

8

i j 

to to 

00 -J 

J

J

&

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"i P P O O P O 

g | | 3 3 § P 

* 1 1 * 1 i- § 

"P. o ft I 1 i ? * 

1 £ 1 & 1 I 

<" < 2 

fa n Op. D. 

w l»i U> > ! ! ! bo 

t»i vO \O 

! ! ! i i ! Lo 

vi

bo bo to ! 4^4>4^4^ I Ln '&*. W O i_n vO ->J 4^- k i ON 

' i ON tn ON ^ i i tO 

OO *». tO \C ON 

>- .1.1. 

i ki to i U> ' to 4^. 

Ov Ut 4^- 9\ VO 

P ' 

! o ! to ! ! 

O\ -J 

1 i 

ON tn to i ! \o ! ! OO 4i> U) OO 

. . J ' ^ 

O\ ^ l>> tO VO i i 

tO NO -|^ -J 00 

p 1 

! ' to 1 1 ! ! u> 

9\ ^^ 

! to 4^. 1 ! ! ! u> 

9\ VO 9\ 

Lft In Ui ' i ! ' to bo 

O\ tO U) ^ HON In ! ! l/i In 4^ ! 4^. 

H-k 00 » 

: ^S 5^ : : : : 

, J , . , , , J .' 

i tO i U> i i i t*> 4^ 

ON U» ON 

.1 .1.1 

i to i U> i I ! w 4^. 

4^-4 O to 

total Arsenic, 

Ln In 

'

bo bo 

UJ O 

to

Ut

'

o

4^ Ct 

vO -J 

p

I

Ln £t 

ON

^-J <I 

tO H-k 

ON tO 

1

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U> u» 

W 4^. 

.1

L> 

u\

c* c~ 

| 3 

3' 5" 

c c 

3 3 

o & 

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n

D.

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p . i 

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o

In In ! 

p

p

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o

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8.

O65

1 , 

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5*

re

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p

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to

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4^ i 

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1

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£S 

"° 3 

0 (D "^ S 

J"

^

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium,

dissolved

Boron,

total

Boron, 

dissolved

Cadmium,

total

Iron,

total

Manganese,

total

Phoshorus,

total

Phosphorus,

dissolved

Strontium, 

total

Strontium,

dissolved
6»iqei eei 

22^

O (JQ (JQ 

S- 3 3 

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3 </5 </5 

c' c° 

£ 3 3 

a o & 

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CD 'O 

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CD

CL

J J .' 

tO CO CO 

<^> .' J 

' to ' Lo U> 

ON tO h- 

.' J , 

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J J 

-~J ON i i 

CO H* 

l l l 

4*. ! ! 

NO

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^3 oo -j to 

J

LA 4^ 4^ 

4>- ON *- 

.'

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tO LO NO 

1 1 1 ON to 4>- 

ON OO 

1

-ON : : 

Lo 5>j ! j 

4>- U) 

Lo 4>- LA 

4*. 4>- LA 

O EC ^»- O 

i i f & 

I 1 f 1 

g g. S 

«-< £-55 

<8 o 

3 <^ 

CD

*-**

J .1 .1 .1 

4^ LA LA Lo 

\O --J LA 4i. 

i i i i 

J J J , J J 

Ni "-J ^ i "-J ^ 

i j i j 

S

i ON In i '-J 

> i t/l 

1 LA ! ! to 

oo

i LA LA LA 

to LA 4^ 

Lo Lo ! LA i 

-0 NO O 

.',.'.

CO CO i LA 

tO ON ON 

i i i i 

1 1 

LA 4>- i i 

ON -O 

J J , J 

4i. ~-J ! LA 

4>- tO LA 

.' ',

' J^ ' ^ 

1 1 ON OO LO K> H- 4^. 

Lo LA ON Lo 

Lo LA o\ 4^ 

00 00 Q 00 T3 j i 

I3 I 3 jj- £' ti. 1 ffi 1 T3 

fill I 

5 & g. 3 

E | | 

^ s 

2. « 

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i) I I 

*4i. 4> to LA ' LA 

LA -fc»- ON to 

II 1 III 

p J J J J J J 

Lo U) Lo Lo U) 4^ 1*) !to ^)^j 

i 1 1 1 1 

ts>i ts>i (/ION itO Lo C*> -~J J 

9\ *J ^--J NO h^NOWLA 

S 0 1 

'SO i LO i 4^ i 

"

rt

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SB

O p , 1 

5 LO LO i LO 4^. i 

g. 4*. LA LO 

"ta. 1

S , , i 

R* i i bo ' 4^. 4> 

« LA OO Ji. 

sS

I i 

la i bo i LA Lo 

a 4*. to oo 

9

e

a

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i U) i l*> i ts> i 1*) i i 

W O OO H- 

.IP . .' 

ON to OO vo ON 

p J , .' 

LA 4^- i ON i --J 

1 NO OO 

^

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0 1 1 1 1 

OLO h-UOVO-J-JOO 

H- . J J 

NO i bo i LA ln 

p ^ . J 

NO i bo i 4^ 

TJ

si

li

11

(D ~ 

*J

^

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium, 

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Iron,

total

Manganese,

total

Phoshorus,

total

Phosphorus,

dissolved

Strontium, 

total

Strontium,

dissolved

1 

2

(D

(0

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c 

3

3

0)

Q

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cB

S5'

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0

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CD

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(D

Q. 

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CO

T3

c5"

T3

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CD

CD" 3,

w

03

Q. 

CD

CD

CD

5T

5"

<

(U

CD-t

5'

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c

T3

T3 

CD

5"

o.

3J

00

to

(n3'

CD

00 

-xl

CD

£

o

3' 

c

CD

Q.
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g> o 

5; cr 

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2. o 

S- P 

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£ £ 

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i i 

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u> Ju 

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10 Lfl 

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C/3

resi olids,

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C/3 C/3 *T3 "T3 O 

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a § S. 2. - S p p C c Ga- o. 3 3 

O H-« * Q^ 

P S g- a* 5* 

2. ^"* o 

PY^ ^ fo 

n> a. 

a.

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jo tO i i i 

oo ON 

i ii i i 

, , ^P ^^ , 

uj in N* 

P . 

u) (>> u> in(^< 4^- -U. K> (>> 

4^ -J <~n Oto oo h- oo t>> 

S 0 ,1 

5Q (^ (jj ' ' i 

§ tO U) 

S3

1 : , , : i 

O

a

^_

^ P 

J» --4 -~4 Lft In --j L/i 

(* K- IO -J OO tO --4 

s§

^

ft o 

a ^j ^-j u> ^-j Ln 

a « i u> u> « i -»4 

a

1

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Pt>> t>> i I I 

ON U) 

i P 

to

P

u> u> in 4^ 4^ 

OO NO OO U) NO 

0

! ii ! to k> 

in in ! ' 4i. 

U) U) 4^ 

P

4^ 4^ i i t>> 

ON NO Ln 

-Q

*f

g (D a) 

 (D 

§ 0 

5 £ §

(D ^ 

3-

Aluminum,

total

Aluminum,

dissolved

Arsenic,

total

Arsenic,

dissolved

Barium,

total

Barium, 

dissolved

Boron,

total

Boron,

dissolved

Cadmium,

total

Iron,

total

Manganese,

total

Phoshorus,

total

Phosphorus,

dissolved

Strontium, 

total

Strontium,

dissolved

3CO

cr

(D

to

CO

c

3

0)

o

8

s

21o'

D

O

O 

(D

o'

Dto* 

O

cr 

«

CD

i

Q. 

0)

0

D

to

3-

52.

8

^

1

CD

a. CD"

to

fi)

Q. 

CD

(D

3

CD

to 

5'

S" I

5'

CD

c

T3

1

5'

o 

to'

5

CD

i?to p'

(O

00

rCO

I

o

5' 

c

CD

Q.
Table 10. Summary of selected trends in element concentrations 

in stream water in the upper Illinois River Basin, 1978-90

[This table includes only those sites with greater than 30 observations and 3 years 

of data, results with a confidence level greater than 90 percent, more than half of the 

number of observations above the detection limit, and little difference between results 

when 0 or the minimum reporting level was substituted for censored observations]

Element

Aluminum, total recoverable

Arsenic, total recoverable

Barium, total recoverable

Barium, dissolved

Boron, total recoverable

Boron, dissolved

Chromium, total recoverable

Copper, total recoverable

Iron, total recoverable

Iron, dissolved

Manganese, total recoverable

Manganese, dissolved

Nickel, total recoverable

Nickel, dissolved

Strontium, total recoverable

Strontium, dissolved

Number of sites

Downward trend Upward trend

2

1

17

12

13

4

0

4

8

1

14

13

2

3

6

7

1

0

1

1

0

0

1

1

1

0

1

0

2

0

15

9

Table 11. Statistical summary of concentrations for selected elements in streambed sediments from the upper Illinois

River Basin, 1978-87

[All concentrations are in micrograms per gram; <, less than]

Percentile1

Element

Period of 

record

Number of 

observations

10 25 50 

(median)

75 90

Arsenic

Cadmium

Chromium

Copper

Iron

Lead

Manganese

Mercury

Phosphorus

Zinc

1978-82 

1978-82 

1978-82 

1978-82 

1978-82

1978-82 

1978-82 

1978-82 

1978-82 

1978-82

Unsieved

54 2.7 3.6 5.5 7.2

80 1.0 1.5 3.0 10.8

105 9.0 17.0 35.0 120

89 11.0 24.0 49.0 130

83 5,280 10,000 16,000 23,000

105 20.0 48.5 130 262

56 290 352 474 573

100 .05 .10 .30 .50

103 334 552 949 1,410

91 50 100 230 510

Sieved (<63 micrometers)

9.1

61.9

444

460

32,000

908

692

2.18

2,570

1,770

Arsenic

Cadmium

Chromium

Copper

Iron

Lead

Manganese

Mercury

Phosphorus

Zinc

1982-87

1982-87

1982-87

1982-87

1982-87

1982-87

1982-87

1982-87

1982-87

1982-87

77

77

77

77

77

77

77

77

73

76

4.1

<.5

10.8

13.0

15,300

14.0

418

.04

534

63.0

5.2

<.5

14.5

17.4

18,700

20.4

480

.06

645

80.3

6.0

<.5

32.0

35.0

24,000

49.0

620

.10

848

145

8.40

1.9

44.0

68.0

29,000

96.0

865

.30

1,500

210

13.0

4.2

78.0

122

34,200

240

1,020

.72

1,990

379

'Percentage of observations with concentrations less than or equal to indicated value.

Table 10 135
Table 12. Tukey studentized range test for ranked concentrations of sieved streambed samples, 1978-87

[<x> is the mean of ranks for the subbasin. "grp" indicates which means can be grouped together; means of concentrations, with the same letter(s) for each ele

different at the 95-percent confidence level]

 

"o"

0)

3

Q.

3

8

m

A

A

l-f

CO5"

0)

Sf

Ia.

I

jl

0)

a

CD

I

(D

Subbasin

Tributaries to

lower Fox River

Tributaries to

upper Fox River

Tributaries to

Des Plaines River

Kankakee River

Little Calumet

River

Lower Du Page

River

East and West

Branches

Du Page River

Des Plaines

River

Salt Creek and

North Branch of

Chicago River

Number of Arsenic

observations <x> grp

10

9

10

4

6

6

10

8

5

Table 13. Tukey studentized

26 a

41 a

36 a

46 a

27 a

23 a

36 a

45 a

32 a

Cadmium

<x> grp

24 a

25 a

28 ab

26 ab

35 ab

32 ab

50 b

52 b

37 ab

Chromium

<x> grp

16 a

14 a

35 ab

29 ab

47 b

33 ab

47 b

44 b

57 b

Copper Iron Lead

<x> grp <x>

14 a 15

16 a 27

28 ab 46

23 ab 42

42 be 41

47 be 18

52 be 38

46 c 44

53 c 50

grp <x> grp

a 10 a

ab 20 ab

b 31 be

ab 33 ad

ab 52 cd

ac 36 bed

ab 43 cd

be 46 cd

be 59 d

Mercury

<x> grp

15 a

22 ab

27 ab

28 abc

43 be

41 be

51 c

45 be

49 be

M

<

4

range test for ranked concentrations of unsieved streambed samples, 1978-87

["n" is the number of observations in a subbasin, <x> is the mean of ranks for the subbasin, "grp" indicates which means can be grouped together; means of con

element in the subbasin, are not significantly different at the 95-percent confidence level; No obs., no observations]

Subbasin

Tributaries to

Fox River

Tributaries to

Illinois River

Upper Fox River

Lower Fox River

Calumet Sag

Channel

Little Calumet

River

North Shore

Channel

Skokie River

Arsenic

n <x> grp

6 14 b

No obs.

9 34 a

18 27 a

No obs.

No obs.

11 10 b

No obs.

Cadmium

n <x> grp

No obs.

No obs.

9 24 a

18 43 b

11 38 ab

10 28 ab

11 67 c

14 20 a

Chromium

n <x> grp

8 13 a

7 19 ab

13 35 be

18 46 c

10 70 d

12 82 de

11 91 e

19 35 be

Copper

n <x> grp

7 13 a

7 14 a

13 26 ab

18 49 c

10 60 cd

No obs.

11 78 d

18 38 be

Iron

n <x> grp

7 31 ab

7 18 a

14 33 ab

17 40 ab

10 37 ab

No obs.

No obs.

19 48 b

Lead Mercury

n <x> grp n

8 18 a 7

7 14 a 7

13 35 ab 13

18 45 b 18

11 74 cd 10

12 48 b 10

11 90 d 10

19 56 be 18

<x> grp

6 a

30 ab

46 be

48 be

67 cd

37 b

87 d

41 b

M

n

n <

6 

No 

12 

18 

No 

No 

11 

No 
Table 14. Relation of trace element concentrations in streambed sediments from the upper Illinois River Basin 

to background concentrations in streambed sediment and average concentrations in soils 

[Concentrations are in milligrams per kilogram except where indicated as percent (%)]

Element

Arsenic

Cadmium

Copper

Chromium

Iron

Lead

Manganese

Mercury

Phosphorus

Zinc

Geometric 

mean

4.4

.1

11.3

8.4

13%

15

430

.04

350

45

confidence 

limits

11.6

1.3

34

25

29%

41

1,474

.15

1,012

111

Geometric 

mean

4.8

13

33

1.4%

14

260

.081

200

40

confidence 

limits

31

102

223

12%

53

3,794

.51

1,741

178

10

2.7

1.0

9.0

11.0

.53%

20.0

290

.05

334

50

25

3.6

1.5

17.0

24.0

1.00%

48.5

352

.10

552

100

50 

(median)

5.5

3.0

35.0

49.0

1.60%

130

474

.30

949

230

75

7.2

10.8

120

130

2.30%

262

573

.50

1,410

510

90

9.1

61.9

444

460

3.26%

908

692

2.18

2,570

1,770

'From Kelly and Hite, 1984.

2From Shacklette and Boerngen, 1984

Percentage of samples with concentrations less than or equal to indicated value.

Table 15. Correlation coefficients between log-transformed element concentrations in sieved streambed-sediment 

samples from the upper Illinois River Basin, 1978-87

Copper Zinc Chromium Mercury Phosphorus Lead Cadmium Iron Manganese Arsenic

Copper 

Zinc 

Chromium 

Mercury

Phosphorus

Lead

Cadmium

Iron

Manganese

Arsenic

1.0 

.95 

.91 

.89

.78

.74

.59

.34

-.33

.19

1.0 

.90 

.90

.71

.81

.55

.39

-.26

.21

1.0 

.82

.72

.73

.68

.43

-.24

.24

1.0

.77

.69

.47

.40

-.23

.29

1.0

.50

.42

.36

-.29

.28

1.0

.50

.34

~~. J

.23

1.0

.22

-.2

.27

1.0

-.4 1.0

.30 .41 1.0

Table 16. Correlation coefficients between log-transformed element concentrations in unsieved streambed-sediment 

samples from the upper Illinois River Basin, 1978-87

Zinc Copper Chromium Cadmium Mercury Phosphorus Lead Manganese Arsenic Iron

Zinc 

Copper 

Chromium 

Cadmium

Mercury

Phosphorus

Lead

Manganese

Arsenic

Iron

1.0

.85 

.85 

.75

.78

.68

.61

-.21

-.05

.31

1.0 

.80 

.69

.69

.51

.66

-.35

-.16

.30

1.0 

.68

.77

.58

.31

-.21

-.10

.22

1.0

.61

.27

.40

-.50

-.28

.24

1.0

.51

.26

-.07

.10

.16

1.0

.52

.37

.42

.40

1.0

-.31

-.12

.40

1.0

.62

.42

1.0

.43 1.0

Table 14 137
Table 17. Factor analysis of log-transformed trace 

element data from streambed sediments of the upper 

Illinois River Basin, 1978-87 

[Factor loadings are multiplied by 100]

Factor loadings

Element

Sieved

Copper 

Zinc

Chromium

Mercury 

Phosphorus 

Lead

Cadmium

Iron

Manganese 

Arsenic

Percent variance explained

Unsieved

Copper 

Zinc

Chromium

Lead

Mercury 

Phosphorus 

Percent variance explained

Factor 1

97 

97

95

91

77 

76

60

43

-24 

30

54

89 

87

86

84

77 

34 

62

Factor 2

-14

-7

-1

-1 

-5 

10

15

16

73 

68

11

25 

40

35

30

30 

94 

28

Table 18. Summary of element concentrations in water, suspended sediment, streambed sediment, 

and biota in the upper Illinois River Basin, 1987-90

[Ranges for total recoverable data represent the total range in concentrations for 40 sites. Ranges for 

suspended-sediment data represent the total range in concentrations for 8 sites. Ranges in streambed-sediment 

data represent the total range in concentrations from main stems and tributaries at 372 sites. Data for biota in 

micrograms per gram dry weight, ug/g, micrograms per gram; <, less than; --, not analyzed for this element]

Concentrations

Element

Aluminum 

Antimony 

Arsenic 

Barium

Beryllium 

Boron 

Cadmium 

Chromium

Cobalt 

Copper 

Iron 

Lead

Manganese 

Mercury 

Molybdenum 

Nickel

Selenium 

Silver 

Strontium 

Vanadium 

Zinc

Total recoverable 

in water 

(WI/L)

<50-49,000

<l-8 

<5-270

<.5-4.0 

<50-950 

<l-62 

<5-420

<5-110 

<5-650 

<50-27,000 

<5-710

<5-l,100 

 c.05-1.7

<5-200

<.!-! 

<3-10 

73-1,800 

<5-33 

<50-1,100

Suspended 

sediment 

Oig/g)

800-99,000 

<. 1-7.4 

<.1-910

<.l-3

<.l-46 

<16-980

<2-34 

.28-990 

600-85,000 

1.8-440

35-10,000

.3-780 

<4-300

<.1-19

<4-150 

9-2,100

Streambed 

sediment

(ng/g)

15,000-83,000 

.3-81 

1.1-140 

57-380

<l-7 

<.4-14 

<2-46 

17-640

6-65 

9-800 

15,000-130,000 

11-1,700

180-7,500 

<.02-6.2 

2-51 

9-130

.1-9.5 

<2-29 

29-1,100 

23-110 

24-3,200

Biota

(^g/g)

3.0-2,100

.2-6.7 

.1-590

2-340 

.3-9.5 

1-11

3.8-210 

110-2,500 

5.0-22

1.9-7,800 

.005-0.5 

1-17 

2-36

.3-7.9 

2-15 

.1-580 

.3-5.6 

34-1,300

138 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Table 19. Element concentrations in streambed sediments from the upper Illinois River Basin as related to pollutional 

classification of Illinois stream sediments

[NAWQA, National Water-Quality Assessment Program; <, less than; >, greater than; mg/kg, milligrams per kilogram, --,]

Breaks in probability 

curves from NAWQA 

Concentration classification (mg/kg)1 streambed-sediment data

Element

Arsenic

Cadmium

Chromium

Copper

Lead

Mercury

Nickel

Zinc

Nonelevated

<8

<.5

<16

<38

<28

<.07

<80

Slightly elevated

>8

>.5

>16

>38

>28

>.07

>80

Elevated

>11

>1

>23

>60

>38

>.l

>100

Highly elevated

>17

>2

>38

>100

>60

>.17

>170

Extreme

>28

>20

>60

>200

>100

>.3

>300

(mg/kg)

10

<2

90

80

40

No observable break

50

200

'Illinois River streambed-sediment classification from Kelly and Kite (1984).

Tablets 139
Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National Wa

the upper Illinois River Basin, 1987-90

[Correlations were done with the concentrations less than the minimum reporting level (MRL) set to zero. Correlations not shown if majority of concentrations 

1o

D)

Q. 

H

m

1

5'

§

s

i

i

a

D)

3 

Q.

00

o

ff

_k 

(O

00

<0

--, correlations with p>0.10

Physical property 

or element

Aluminum Antimony Arsenic |

a> m

Cadmium Chromium Cobalt Ia.

8

1

 o

3

Manganese Molybdenum

£

u

z

All 8 sites combined

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

Chromium

Cobalt

Copper

Iron

Lead

Manganese

Molybdenum

Nickel

Phosphorus

Silver

Vanadium

Zinc

Discharge

Calcium

Sodium

Potassium

Suspended sediment

concentration

Carbon, organic total

Percent of sample

<.062 mm

Particle surface area

1

.3

.34

.81

~

.52

.57

.19

.68

.22

.54

-.19

~

.98

.15

.18

-.89

-.25

.87

.31

-.16

.29

.78

0.3

1

.38

.3

.77

.72

.63

.74

.35

.7

.15

.49

.74

.57

.8

.35

.8

.34

-.32

.25

.23

-.28

-.32

~

.13

0.34

.38

1

.27

.23

.29

.52

.14

.67

.45

.23

.33

.22

.41

.29

.27

-.43

-.18

.13

--

-.24

~

.48

0.81

.3

.27

1

.12

.48

.46

.16

.51

.17

.48

~

.82

.13

.17

-.7

-.21

.72

.2

-.16

.25

.59

0.77

.23

.12

1

.68

.52

.77

.2

.79

.15

.45

.69

.7

.84

.11

.82

.44

.23

_

-.33

-.2

-

-.1

0.52

.72

.29

.48

.68

1

.7

.75

.41

.65

__

.62

.95

.53

.66

.55

.73

.42

-.5

.13

.57

-.17

-.22

.22

.26

0.57

.63

.52

.46

.52

.7

1

.57

.71

.45

.53

.54

.78

.33

.55

.63

.62

.24

-.62

-

.52

-.22

-.45

--

.5

0.19

.74

.14

.16

.77

.75

.57

1

.29

.82

__

.69

.77

.64

.81

.21

.86

.4

-.2

.4

.3

-.28

-.14

.11

0.68

.35

.67

.51

.2

.41

.71

.29

1

.39

.41

.48

«

.19

.7

.32

.3

-.72

-.2

.51

.12

-.28

~

.72

0.7

.79

.65

.45

.82

1

.13

.53

.65

.76

.8

.81

.35

.38

_

-.43

-.15

-

-.26

0.15

.45

.15

.53

.39

.13

1

.13

.2

.22

_

.22

-.12

-.12

-.12

-.11

-.37

-.29

-.12

.23

0.22

.49

.23

.17

.45

.62

.54

.69

.41

.53

..

1

.66

.36

.52

.23

.68

.19

-.28

.47

.41

-.18

-.21

-

0.

.

.

.

.

.

.

.

.

.

.

.

1

.

.

.

.

.

-.5

.

.

-.1

-.3

.

.

Kankakee River at Momence, 111. (site 14)

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

.57

1

.52

.5

.52

1

-.38

.57

.57

-.38

1

.5

.57

1

.69

.36

.51

.38

.46

.68

~

.42

.4 .41

.8 .33

.39 .38

.79

-.52

.52

.

.

.
Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National Wa

the upper Illinois River Basin, 1987-90 Continued

Physical property 

or element

Aluminum Antimony 'E Beryllium Cadmium Chromium

1

Ia.

S

| I

Manganese Molybdenum j> 

o 

Z

Kankakee River at Momence, 111. (site 14) Continued

Chromium

Cobalt

Copper

Iron

Lead

Manganese

Molybdenum

Nickel

Phosphorus

Silver

Vanadium

Zinc

Discharge

Calcium

Sodium

Potassium

Suspended sediment

concentration

Carbon, organic total

Percent of sample

<.062 mm

Particle surface area

0.69

.38

~

~

.74

-.34

.95

.75

-.92

-.49

.83

.56

-

~

.79

0.36

.46

.4

.41

.38

.35

.4

.34

.52

.32

~

_

--

~

~

~

_

0.68

~

.8

.33

.79

.78

.76

_

.54

«

~

-.32

-.41

-.54

-.44

-

0.51

--

-.52

.51

-.31

-.48

.57

.58

-.57

-.53

.55

.52

~

.31

.53

_

0.42

~

.39

.38

.52

.39

.46

_

.53

-

-.42

-.41

-.56

--

-

1

.31

-

._

.33

.77

~

-.31

.69

.68

-.71

-.31

.62

.32

~

-

.55

0.31

1

.31

.8

.35

.72

.66

.74

.31

.47

.52

.55

-.47

_ o

_

--

-.53

-.31

.58

_

0.31

1

.45

.59

__

.51

.31

--

_

.34

.3

_

-

-

~

-

Iroquois River near Chebanse, 111

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

Chromium

_i Cobalt

S- Copper

» Iron

§ Lead

1

.35

.69

~

.45

.83

.35

1

.45

.29

~

.29

.29

--

.42

.37

__

.45

1

__

.27

.32

.29

.69

.29

1

~

.38

.29

.33

.74

__

1

.31

.35

.34

.41

.45

.29

.38

.31

1

.5

_

.29

.27

.29

.35

..

1

-

.28

~

_

.33

.34

1

.36

.5

__

0.8

.45

1

.45

.75

.44

.89

.46

.32

.51

.33

-.33

~

_

-

-.51

-

.42

. (site 28)

.83

.42

.32

.74

~

.5

.28

.36

1

0.35

.59

.45

1

_.

.38

.31

.34

~

_

.53

.38

.3

_

-

-.46

-.38

-

_

.37

.29

.41

..

.5

1

_

0.72

.75

--

1

--

.86

.53

_

.47

-

~

-.47

-.63

-.64

-.41

-

-.36

~

~

.39

..

.78

-.32

0.33

.51

.38

__

1

.34

«

_

.38

.31

.38

-

~

-.36

~

_

.35

..

.51

0.7

.

.

.

._

.

1

~

.

.

.

-.8

 4

.

-

~

~

.

.

.

.

.

.7

.

.

.
£ Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National W

10 the upper Illinois River Basin, 1987-90 Continued

0) "5"

0)

3

_i Physical property 

3 or element

o

9

m

3 Manganese

w Molybdenum

= Nickel

^ Phosphorus

§f Silver

» Vanadium

~ Zinc

n Discharge

3. Calcium

o> Sodium

Q.

2 Potassium

2. Suspended sediment

"^ concentration

jo Carbon, organic total

J> Percent of sample

§ <.062 mm

Particle surface area

E

3 

C

E

a

>.

1 E ^P OT

c Jr 

< ^

E E

3 3

| |

00 O

|

| 

O

o § o 8

c "O 

o S?

IQ)

1

i

1 

>> z

o

Iroquois River near Chebanse, III. (site 28) Continued

-0.36

.42

-

~

.88

.38

-.65

-.61

.35

.41

.37

.64

._

0.35

0.29

.29

.39

.55

..

..

..

..

-

~

.37

0.39

0.52 .45

..

--

.83

.27

-.37 .36

-.34

.56

.28

-

.36

.52

0.71

.48

~

-

.32

.48

0.78 -0.32

..

.35

.42 .28

.3

.39

-.5 .44

.38

.51

-.42

..

0.51

0.51 .32

.36 .33

.28

.84

.55

.38

-.49

-.65

~

..

.52

i~

.39

~

_

-.67

.66

.26

-.7

-.5

--

-.48

__

1 0.

.31 1

--

.

.3 .

..

__

-.3

.

-

..

.

.

Des Plaines River at Riverside, III. (site 40)

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

Chromium

Cobalt

Copper

Iron

Lead

Manganese

Molybdenum

Nickel

Phosphorus

Silver

1

-

.52

__

.44

~

.88

~

._

.32

1 .36

.36 1

.4

.34

_

.48

.34

-

.4

.45

.52

..

.4 .34

i

1

.36

.54

.38

.63

--

..

.41

_

.36

1

.46

.39

.37

.6

.48

.29

.44

.48

.54

.38

.46

1 -.3

-.3 1

.66

--

.7 -.55

_.

.39

.52 -.42

.42

.88

._

.34

.63

.39

.66

_.

1

1

._

.45

_

.37

.7

-.55

~

1

.8

«

_

.4 .

~

.

.

-

1 .

.43 1

._
Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National W

the upper Illinois River Basin, 1987-90 Continued

&

Physical property

or element

E

3 

C

E

_3

^

§

1

a E

1 .2

I t

E E 3 3

1 I o 5

i &

3 °

«= "8

A 

£ $

a> E

3) 3

Q) C 

C Q)

CO "D

? \

CO TT 

SO

5

« 

o

z

Des Plaines River at Riverside, 111. (site 40) Continued

Vanadium

Zinc

Discharge

Calcium

Sodium

Potassium

Suspended sediment

concentration

Carbon, organic total

Percent of sample

<.062 mm

Particle surface area

0.94

-.45

-.41

.81

-

-

.42

_

0.42

--

-.29

-.36

--

~

--

0.38 0.59

__

..

_.

~

.35

--

~

.33

._

0.49 0.34

.31 -.3

._

-

__

--

--

.36

0.56

.35 0.34

.34

-.34

~

_

-.5 .32

--

.49 -.47

0.89

0.31

-.36

-.43

-.31

.61

--

-.35

.46

_

..

-0.47

-.45

0.47

_

-.74

..

.43

_

~

_

-

-

~

Chicago Sanitary and Ship Canal at Romeoville, 111. (site 55)

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

Chromium

Cobalt

Copper

Iron

Lead

Manganese

Molybdenum

Nickel

Phosphorus

Silver

Vanadium

Zinc

Discharge

Calcium

Sodium

1

-.37

.65

_

..

.86

~

-.7

-.34

~

.92

~

-.69

-.83

-.37

1

.31

-.4

.35

.3

.33

~

..

.28

.35

~

.35

-.38

-

.65

.31 -.4

1

1

--

.31

.32

.49

-

._

-.44

.64

.29

-.37

-.49

__

.35 .3

.31

1 .72

.72 1

.44

.75 .64

._

-

_.

__

.66

.44 .7

.7 .83

_

.82 .63

_.

-.33

-.39

_

.33

.32

.75

.44 .64

1

1

.52

~

.91 -.3

__

.49

.48 .42

.74

.37 -.35

.77

.29

-.49

-.32

.86

._

__

.49

~

_.

.52

._

1

1

.4

-.66

~

.77

__

-.77

-.86

-.7

.28

-.44

_

.91

 3

.4 -.66

~

1

1

.4

.41

-

.32 -.63

-.35

-.42 .58

.65

-0.

.

~

-

.

.

-

-

.

1

.

.

_

-

-
Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National W

the upper Illinois River Basin, 1987-90 Continued

1 t

to 

H Physical property

3 or element

0)

m

a

a, Potassium

2. Suspended sediment

' concentration

jf Carbon, organic total

<if Percent of sample

^ <.062 mm

£ Particle surface area

3

§ Aluminum

°- Antimony

~ Arsenic

5? Beryllium

"_i Cadmium

<o

T° Chromium

§ Cobalt

Copper

Iron

Lead

Manganese

Molybdenum

Nickel

Phosphorus

Silver

Vanadium

Zinc

Discharge

Calcium

Sodium

Potassium

Suspended sediment

concentration

Carbon, organic total

Percent of sample:

<.062 mm

Particle surface area

E

3 

_C

i

c

c

u'c

E E

3 3

1 1

0) (0 

CD O

E

s a,

E S

I s

o

i

Q.

5

£

_ 0)

c s c

O S, " 

(0

s

§ a

E «

> 2

o

s

Chicago Sanitary and Ship Canal at Romeoville, III. (site 55) Continued

0.54

.3

.46

.82

-0.5

-

--

~

_

0.42

~

-

0.29

0.3

._

~

.46

-0.33

-0.32

-.37

..

.46

_

--

0.36

-

0.45

-0.36

-.4

.46

.81 0.41 .41

-0.32 -0.4

-.3

-.3

~

-.56

Du Page River at Shorewood, III. (site 69)

1

.57

.68

.61

.5

.38

.91

-

.58

-.57

.96

.4

-.84

-.6

.86

.59

.45

.41

.81

_

1

.64

.29

.36

.41

.44

.34

.43

~

..

~

.58

-.29

.39

.39

.3

~

.29

.38

~

~

.57

.64

1

.56

.56

.56

.41

.67

--

_.

.61

-.45

.33

.73

.53

-.53

--

.47

.49

«

-

.55

.68

.29 .36

.56

1

1

.46

.34

.39 .5

.74

--

._

..

.44 .37

-.49

.61

.73

.47

.39

-.55

-.33

.64

.33 .34

.3

.54

.61 .5

.41 .44

.56 .56

.46 .34

..

1 .73

.73 1

.58 .58

.71 .65

.36 .41

.55

_.

.73 .73

..

.29 .55

.65 .55

.43

._

-.61 -.49

-.31 -.29

.63 .54

.52

.32

.47 .42

.38

.34

.41

.39

.5

.58

.58

1

.55

.63

..

.69

.61

.41

.57

-.34

--

.41

--

-

.91

.43

.67

.74

._

.71 .36

.65 .41 .55

.55 .63

1

1

1

_.

.71 .46

-.46 .31 .58

.3 .44 .42

.94

.46 .5

.38 -- -.27

-.74

-.44

.85

.47

.33

.37 .38

.68

.

.

.

.

.

.

.

.

.

.

._

1

1

.

.

.

..

-.4

.48

.3 .

.

~

.

.
Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National W

the upper Illinois River Basin, 1987-90 Continued

Physical property 

or element

Aluminum Antimony Arsenic Beryllium Cadmium Chromium

i

o 

U 0

1

 o Manganese Molybdenum

u 

z

Illinois River at Marseilles, 111. (site 76)

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

Chromium

Cobalt

Copper

Iron

Lead

Manganese

Molybdenum

Nickel

Phosphorus

Silver

Vanadium

Zinc

Discharge

Calcium

Sodium

Potassium

Suspended sediment

concentration

Carbon, organic total

Percent of sample

<.062 mm

Particle surface area

1

-.64

.4

.56

-.29

-.51

-.66

.87

-.63

__

-.5

-.58

-.67

-.46

.97

-.65

.49

-.75

-.82

.69

.47

-

.79

-0.64

1

-.31

.66

.59

.34

.5

-.62

.66

._

.36

.7

.51

.53

-.61

.59

-.52

.57

.53

-.52

-.37

--

-.46

0.4

-.31

1

.3

-.33

-.3

-.61

.57

-.43

.31

-.32

-.33

-.29

.43

.36

-.33

-.45

_

.29

~

-

.42

0.56

--

.3

1

_

-.48

.58

-.29

-.35

~

~

.55

-.37

~

-.33

-.55

.37

--

-

-

.56

-0.29

.66

-.33

1

.51

.35

-.47

.37

--

.5

.4

.63

_

.47

.34

--

_

--

-

-

-0.51

.59

-.3

.51

1

.48

.64

-.5

.68

__

.29

.72

.72

.74

-.44

.42

-.51

.36

.36

_

-.36

~

-.33

_

0.34

.48

1

.44

.72

.64

.59

.46

_

.32

-.61

--

_

-.53

~

-0.66

.5

-.61

-.48

.35

.64

1

-.57

.56

__

.62

.67

.52

.51

-.61

.64

-.34

.54

.71

_

-.32

--

-.58

0.87

-.62

.57

.58

-.47

-.5

-.57

1

-.55

._

-.35

-.5

-.46

-.43

.88

-.5

.46

-.58

-.72

.61

.41

--

.71

-0.63

.66

-.43

-.29

.37

.68

.44

.56

-.55

1

.37

.65

.69

.72

-.57

.49

-.62

.54

.52

_

-.47

--

~

-.41

_

~

0.31

--

_

.72

-

~

1

.28

.27

--

__

-.37

--

-.38

-.36

--

~

-0.5

.36

-.32

-.35

~

.29

.62

-.35

.37

1

.4

.3

.28

-.46

.54

.54

.7

__

--

~

-

-.48

-0.5

.

-.3

.

.

.

.

-.5

.

.

.

1

.

.

-.4

.

-.6

.

.

_

-.4

-

-

-.2

Aluminum 

_i Antimony 

8- Arsenic 

» Beryllium

Cadmium

.31

.33

.59 

.33

Fox River at Algonquin, 111. (site 89)

.46 .65 .42 .55

.39

.44 -- - .48

.34 

.43

.38 

.46

.
7i Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National Wa

5 the upper Illinois River Basin, 1987-90 Continued

0) "5"

0)

H Physical property 

3 or element

« 

m

(D

3 Chromium 

* Cobalt

3 Copper

< Iron

5? Lead

«? Manganese

§= Molybdenum

g Nickel

j* Phosphorus

o> Silver

Q.

5 Vanadium

§ Zinc

-^ Discharge

w Calcium

co Sodium

Potassium

Suspended sediment

concentration

Carbon, organic, total

Percent of sample

<.062 mm

Particle surface area

Aluminum

0.46 

.65

.42

.55

.34

.38

--

.67

-

.39

.83

~

~

~

.67

-

~

.4

c

*!

0.39

.43

-

.46

.42

-.35

.39

-

-.45

-.41

~

o E

'E -2

< m

0.44

.48

~

.46

.51

.36

.43

.44

-.51

--

 5

~

Cadmium Chromium

! 1 & s

1

 o

3

Fox River at Algonquin, 111. (site 89) Continued

1 0.42 -- 0.36 

.42 1 0.62 .71 0.46

~

~

0.58

~

«

~

-

-.4

-.45

~

.36

~

.45

.53

.44

.31

.55

-.38

~

.31

-

-

.36

.62 1

.71

.46

.36

.58

.72

.51

.33

.56

-

--

--

Fox River at Dayton

Aluminum

Antimony

Arsenic

Beryllium

Cadmium

Chromium

Cobalt

Copper

Iron

Lead

1

.49

.67

--

~

.47

.75

.34

.96

.47

.49

1

.44

-

.65

.3

.35

.54

.52

.62

.67

.44

1

-

~

.43

.33

..

.65

_

.65

1

.29

_

.58

.37

.54

.47

.3

.43

-

.29

1

.56

.45

.51

.75

.35

.33

.56

1

.51 1

.75

.47

.46

.58

.54

.53

.3

-

.42

.5

.58

-

~

-

.46

1

.5

.38

.46

.56

-

.6

.47

--

.41

-

-.4

-.36

-

.58

.5

1

.31

.53

.4

.41

.48

--

-

-

Manganese

0.45 

.36

.38

~

1

.44

.52

~

-.42

_

-.44

-.4

~

.44

Molybdenum

0.58

.54

.46

.31

1

.41

-.37

.42

.63

.39

~

-

~

u

Z

0.

.

.

.

~

.

1

-

.

.

-

~

-.3

.

-

~

~

.

, 111. (site 99)

.34

.54

~

-

.58

.45

.51

.37

.53

.96

.52

.65

--

.37

.51

.75

.37

1

.54

.47

.62

~

.54

_

.47

.53

.54

1

_

-

.3

-

.29

.34

.37

_

-

-

~

_

.

.

.

~

.

.

.

.

.
Table 20. Summary of correlation coefficients for physical properties and elements in suspended sediment at eight National W

the upper Illinois River Basin, 1987-90 Continued

E

3 

C

E 

Physical property 2

or element

c

33

.2

1

E E

3 3

1 1 0) (0 

CO O

E

.3

U

8 A

8

Fox River at Dayton, III.

Manganese

Molybdenum

Nickel 0.64

Phosphorus

Silver .48

Vanadium .91

Zinc .37

Discharge .45

Calcium -.84

Sodium

Potassium .74

Suspended sediment

concentration

Carbon, organic total

Percent of sample

<.062 mm

Particle surface area .74

0.35

~

.64

.38

.47

.41

-.56

.36

.34

~

~

~

.43

0.3

.39

.34

.58

~

-.47

.33

--

-

~

.57

0.29

.74

.66

.4

-.36

~

_

-

-.43

.48

0.34

.84

.45

.6

.48

-.49

-

.41

~

--

.56

0.75

-.44

.55

.87

.4

.64

-.76

~

.83

.37

«

-

.62

Ia. £

Q. O

8

 Q

3

« E

3) 3

0> C 

C Q>

a -a 

O) 2

2

m "o

Z

"

u 

z

(site 99) Continued

0.37

0.43 .64

..

.53 .66

.43 .87

.42 .42

.47 .6

-.59 -.84

--

.48 .73

-

--

.35 .8

_.

0.4

.61

.39

.63

.57

-.51

.53

.55

-

-.59

-.46

.36

1

1

.51

.43

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_

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--

.42

0.

1

-.

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-

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fl) 

10

o
Basin, Illinois River1987 high-order in thesediments Correlation forselected streambed Table21. coefficients elements atstreams upper 

Colman Sanzolone, 1991] level; modified from andsignificant correlation the0.10 [--, not atp = 

OUI.Z

uumpeueA 

uimiuojis

J3A|!S

uumuaias 

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uinuapqA|O|/y 

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pean

UOJ|

jdddoo 

Jieqoo 

uimuuoJiio 

lunjiupeo 

uojog 

uinj||Ajag 

uunueg 

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uunujuuniv

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r- r- ON en o 

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r

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CS 0 VO < en CN | cs cs

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m en vo r>-

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-H -^ CS

r«- \o r>- j j

rf cs ON in I-H ^- cs -H -^- vo

1

oo vo O O 

r>- «n oo j cs

OO ^H ^H -^>

«n j cs >o r>-

1

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ON m -^- -H 

vq «n oo rs j

00 ON -H -^- ^H 

o; oi oi oj o;

ON r>- oo O ON 

\o o< en m t~-

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O i-< Ol OO r«- «n r- j ^

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«n j j TT ON

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m TT vo ON «n o< r>- vo -* >n

1 1 1 1

r~ TT en 

j «n »n en «n

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\o -H r«- vo ^r 

r>- 01 01 -H

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TT Ol 01 01 j

r r

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oo j | en TT

5 | | | I

r

o TT r~ oo -<fr ON 01 01 TT «n

Tt ^H m oo 

en \o vo j 01

1 1 1

01 ^H m ON j TT TT

01 O 01 00

m vo in j m

1 1 1 

v~> vo r>- ON

OO -H 1 O< 1-H

1

^^ ON O en ON 

t~- o< en in »n

>n o 

^ ! ! <1 I

rf m rf en * «n * j 01

1 1 1

-* »n >n <o m 01 01 ^H j

1 1

-H 00

! : ^ ^ :

ON oo vo 

r«- j j en m

O en * en oo 01 r>- vo oi «n

1 1 1 1 

'i-s o

aoS _ 

S && 

.B&2 

S c c c

o 'o ^ ^ ^ 

.S "c3 S3 S 3 

NUUUU

o r~ ^r

00 01 TT

1

r«-

! °° !

00 1-H -."n :

i

r>- -^ oi 

vo 01 «n

1

oo vo 

«n j ^r

v~> v~> «n

vo >n «n

1 

-H »n >n

"* 01 '

r

oo r>- oo

VO 01 TT

1

«n vo ON

01 01 <

r r

oi r~ r~ 

r>- -H «n

1

oo 

m ^r j

r~ r~ ^ 

r>- ono

1

01 00 

01 VO j

oo en r>- 

vo «n --3-

1

ON OO 

VO J V~)

r

VO vo ^t

^- i i i i

r

o o o en t~- m

1

ON r~

OI Ol j

ON

 * O 00 

\0 01 TT

Phosphorus 

Potassium .88Sodium --- 

148 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Table 22. Correlation coefficients for selected elements in biota from the upper Illinois River Basin, 1989 and 1990

[Correlations not shown if majority of concentrations for an element were below the minimum reporting level (MRL). Correlations were done twice, first wit

MRL, and second with those values set to zero. If two coefficients are shown, the first represents the correlation where the below MRL values were set to the 

represents the correlation where the below MRL values were set to zero. , correlations with p > 0.10]

fl>o-

(D

IS) 

IS)

1 | E I =

1 | | | I 

Element < m

Aluminum 1 .00

Arsenic 1 .00

Barium -- -- 1.00

Beryllium -- -- -- 1.00

Boron - -- -- -- 1.00

Cadmium

Chromium

Copper

Iron

Lead

Manganese .29

(.34)

Mercury

Molybdenum

Nickel

Selenium

Silver

Strontium .44

(.45)

Vanadium .32

(.38)

Zinc

Aluminum 1 .00

Arsenic -- 1 .00

Barium -- - 1.00

Beryllium -- -- -- 1.00

Boron -- - -- -- 1.00

1 1 1 I ! ! 1 ! I 

o 5 ° s S i 

Common Carp, 1989-90

1.00

1.00

.5 -- 1.00

(.40)

1.00

1.00

.47 - -- 1.00

.56 .38 -- -- 1.00

i.oo

i.oo

.76 -- .50 -- -- - - -- -- 

(.69)

.37 -- -- .46 .34 -- -- 

(.45) (.37)

.31 -- .54 .42 -- -- .53 -- -- 

(.29) 

White Sucker, 1990
-i Table 22. Correlation coefficients for selected elements in biota from the upper Illinois River Basin, 1989 and 1990 Continued

Major and TraceElements inWater, Sediment, andBiota, 1978-90

Element

Cadmium 

Chromium 

Copper 

Iron 

Lead

Manganese 

Mercury 

Molybdenum 

Nickel 

Selenium

Silver 

Strontium 

Vanadium 

Zinc

Aluminum 

Arsenic 

Barium 

Beryllium 

Boron

Cadmium 

Chromium 

Copper 

Iron 

Lead

||eicilfc e ,|j'i,

|<^I"55 5i:fl Is|2|(

White Sucker, 1990 Continued

1.00 

1.00

i.oo 

i.oo 

i.oo

i.oo

.83 - -- -- 1.00

i.oo 

i.oo

.66 .70 -- -- -- -- -- 

.99 -- -- -- .88 -- -- 

Crayfish, 1990

1.00 

1.00 

.51 1.00 

1.00 

1.00

1.00 

.63 -- -- -- -- - 1.00 

-.67 -- -- -- - - 1.00 

.88 -- - -- -- -- .76 -- 1.00

i.oo

Manganese -.74 

Mercury 

Molybdenum 

Nickel

Selenium

Silver 

Strontium 

Vanadium 

Zinc

.65 -- -.64 

(-.69)

-.63

.55 

(.52)

.62

1.00

1.00

-.64 -- 1.00 

(-.58) 

.55 -- -- -- 
Table 23. Correlation coefficients observed in physical properties and elements in water and suspended sediment from the eigh

fixed sites in the upper Illinois River Basin, 1987-90

[Correlations were done with the concentrations less than the minimum reporting level (MRL) set to zero. Correlations not shown if majority of concentration

--, correlations with p > 0.10]

Element in suspended sediment

o-

»

ro w

Physical property or

element in water

Aluminum, total

Aluminum, dissolved

Antimony, dissolved

Arsenic, total

Arsenic, dissolved

Barium, total

Barium, dissolved

Beryllium, total

Beryllium, dissolved

Boron, total

Boron, dissolved

Cadmium, total

Cadmium, dissolved

Chromium, total

Chromium, dissolved

Cobalt, total

Cobalt, dissolved

Copper, total

Copper, dissolved

Iron, total

Iron, dissolved

Lead, total

Lead, dissolved

Manganese, total

Manganese, dissolved

Mercury, total

Mercury, dissolved

Molybdenum, dissolved

Nickel, total

Nickel, dissolved

uminum

<

0.55

.18

~

-.15

_

-.30

~

_

.14

.25

--

.20

.25

.48

.16

.20

.15

.26

._

.30

.12

tntimony

^

_

-0.12

.58

.13

-.65

-.70

-

--

.47

.45

.58

.25

.15

-

_.

.30

.10

.42

-.23

.44

--

.33

.47

.47

'E

0.11

.14

-.17

-.16

-.29

~

-.24

-.24

.14

.11

.17

--

_

.11

.31

.11

.14

.36

.55

_.

~

.22

E

3 

0)

CD

0.44

.14

~

-.13

_

-.31

.10

.21

.27

-

.15

.28

.35

.15

.18

.12

.21

--

.30

.10

| 

1

O

-0.11

.63

--

.20

-.61

-.60

--

.39

.38

.60

.21

.19

--

-.13

.21

-.12

_

.38

-.19

.34

..

~

.26

.42

.46

hromium

O

0.17

.62

.16

-.58

-.71

~

.43

.40

.58

.23

.32

--

_

.31

~

.15

.39

-.11

.44

.22

.58

.57

Cobalt

_

0.39

~

-.56

-.51

.29

.27

.24

.20

--

_

~

_

..

.58

-.16

.28

.39

.40

1 

O

_

.-

0.60

.15

-.62

-.68

-

.49

.47

.59

.27

.18

-

_

.33

-

.12

.41

-.18

.44

_.

.26

.46

.50

|

0.23

-.26

-.21

-.33

-.12

-.16

.13

--

.11

.40

_

.27

.55

..

.22

.13

 o

ro

-0.23

.67

.23

-.66

-.59

-

~

.46

.45

.52

.18

~

-.14

.20

--

-.25

.35

-.32

.32

._

.21

.39

.46

anganese

5

-0.39

-.34

~

_

-.23

-.11

--

-.20

-.35

-.28

-.21

-.32

.35

-.19

.24

Jybdenum

o

0.36

-.54

-.61

.43

.41

.44

.21

.12

--

_

.23

~

.11

.30

.65

._

.39

.36

.34

-

-

-
Table 23. Correlation coefficients observed in physical properties and elements in water and suspended sediment from the eig

fixed sites in the upper Illinois River Basin, 1987-90 Continued

Major and Trace

m

(D

(D

r*

(0

5'

Q)

(D

I

I

Q)

a

00

I

<J»

§

Element in suspended sediment

Physical property or 

element in water

Phosphorus, total

Phosphorus, dissolved

Selenium, total

Selenium, dissolved

Silver, total

Silver, dissolved

Strontium, total

Strontium, dissolved

Vanadium, total

Vanadium, dissolved

Zinc, total

Zinc, dissolved

Discharge

Specific conductance

PH

Temperature

Dissolved oxygen

Hardness

Alkalinity, total

Calcium, total

Calcium, dissolved

Magnesium, total

Magnesium, dissolved

Sodium, total

Sodium, dissolved

Potassium, total

Potassium, dissolved

Chloride, dissolved

Solids, residue on

evaporation at 180°C

Solids, total suspended

Solids, volatile

Carbon, total organic

Aluminum

0.15

.30

~

.39

--

-.31

-.34

.32

--

.11

.19

-.45

-.11

-.17

-.10

-.53

.14

.14

-.40

-.42

--

.11

~

.23

-.24

Antimony

0.55

.61

_.

--

-.15

-.15

.21

.36

.20

-.57

--

-.34

-.33

~

-.18

-.11

-.53

-.51

.43

.43

.49

.47

.34

.16

-.30

-.27

-.20

Arsenic

-0.18

-.14

~

.11

--

-.52

-.50

--

.30

-.24

-.45

-.14

-.22

-.17

-.50

--

__

-.50

-.48

-.27

-.28

-.20

-.25

-.31

-.20

-.13

-.20

Beryllium

0.17

.26

.35

.11

-.20

-.25

.29

.17

~

-.35

-.14

-.11

-.14

-.52

--

-.33

-.36

.14

.13

_.

-.12

Cadmium

0.41

.43

-.15

-.13

-.14

--

.12

_.

.44

.15

-.44

-.31

-.35

-.28

-.20

-.46

-.42

.38

.37

.36

.38

.30

~

-.23

-.17

-

Chromium

0.50

.56

.10

-.26

-.27

.14

-

.18

.41

.11

-.65

-.46

-.40

-.76

-.22

-.16

-.61

-.59

.33

.32

.40

.36

.24

~

--

__

-.18

a

0.19

.37

_

.11

-.28

-.28

--

.24

.12

-.57

-.16

-.23

-.11

-.59

.12

.19

-.53

-.48

.19

.18

.22

.22

.11

.14

.13

-.26

-.36

1

s

0.58

.59

-.14

--

-.13

-.14

-

.19

.40

.25

-.49

~

-.34

-.29

-

-.14

_

-.47

-.45

.48

.47

.49

.48

.38

.21

-.23

-.18

-.16

I

~

0.24

--

-.54

-.54

.10

--

.31

-.12

-.47

-.22

-.17

.26

.28

-.53

-.51

-.18

-.21

_

-.14

-.24

-

-.19

-.36

 o 

a

0.51

.52

-.19

-

.10

-.13

.13

.35

.30

-.42

-.12

-.27

-.28

-.27

-.20

-.34

-.30

.51

.50

.44

.49

.44

.22

-.25

-.16

~

Manganese

-0.27

-.12

-.15

_

-.27

--

-.14

._

-.14

.11

~

.26

«

.31

.37

~

~

~

-.12

.17

~

-.11

-.21

Molybdenum

0.50

.55

_.

--

-.24

-.23

--

.21

.11

.19

.18

-.57

-.37

-.18

_

-.48

-.46

.38

.36

.44

.42

.27

.15

-.24

-.31

-.26
Table 24. Correlation coefficients for median measurements of physical properties and concentrations of elements in water and 

Illinois River Basin

[Correlations were done with the concentrations less than the minimum reporting level (MRL) set to zero. Correlations not shown if majority of concentrations 

-, correlations with p > 0.10

Element in streambed sediment

Physical property or 

element in water

Aluminum, total 

Aluminum, dissolved 

Arsenic, total 

Arsenic, dissolved 

Barium, total

Barium, dissolved

Boron, total

Boron, dissolved

Chromium, total

Copper, total

Iron, total 

Iron, dissolved 

Manganese, total 

Manganese, dissolved

Nickel, total

Nickel, dissolved

Phosphorus, total

Phosphorus, 

dissolved 

Strontium, total 

Strontium, dissolved

Hardness 

Carbon, total organic

n o *c 3 

£ - w "c 

- 5 < 

0.55

-0.44 -.45 -0.40

-.51 -.51 -.41

.33

.34

.51 .61 - 0.33

_ . _

.47 -- .35

.37 .63 -- .43

.33 .49 -- .36

-

.35 -- .33

-.40 -- -- -.48 

-.37 -- -- -.48

-.43

7O

Beryllium

0.32

-.33

-.43

.62

.62

.66

.58

.51

.66

.50

.48

.57

«= ! .2

SEE o -5 o

CO ^ £ 

0 o

A 1/i

.51 0.43 

.65

-.41 -.56

-.42 -.62

0.68 -- .43

.67 -- .43

.41 .73

.66 -- .31

.35

.34

.33 .46 .74

.49 .59

.74 -- .38

.70 -- .42

.36 

.36

-.55 -.49

Cobalt

_

0.52

.50

.35

.58

.44

.44

.48

.47

.55

O

0.63 

.70

-.53

-.58

.54

.56

.66

.37

.75

.58

.50

.49 

-.46

8

«= TJ 1 o y ts 

£. o> o> 

-J c

(0

0.66 

.81 

-.41

-0.33 -.45

.46

.45

.37 .48 -0.35

.43

.32 

33

.52

.41 .55

.34 .43

.42

.49

-.37

35

-.59 

-.51

3 

0)

0.56 

.78 

-.39

-.41

.39

.39

.43

.35

.52

_

.48

.45

-.39

Molybdenum

0.31

_

.77

.77

.51

.78 

.33

.52

.59

.44

.73

.75

--

£o

z

-0.

-.4

-.
Table 25. Correlation coefficients for 90th-percentile measurements of physical properties and element concentrations in wate

upper Illinois River Basin

[Correlations were done with the concentrations less than the minimum reporting level (MRL) set to zero. Correlations not shown if majority of con

were below the MRL. , correlations with p>0.10]

"o"

to

a.

3

o 

o

m

o 

jjf

5'

^

1

w

3

§

to

a.

00o'

(O

r

8

Element in streambed sediment

Physical property

or element in water

Aluminum, total

Aluminum, dissolved

Arsenic, total

Barium, total

Barium, dissolved

Boron, total

Boron, dissolved

Chromium, total

Chromium, dissolved

Copper, total

Copper, dissolved

Iron, total

Iron, dissolved

Lead, total

Manganese, total

Manganese, dissolved

Nickel, total

Nickel, dissolved

Phosphorus, total

Phosphorus, dissolved

Strontium, total

Strontium, dissolved

Vanadium, total

Zinc, total

1 £ .2

.- § S

3. °c <

< <

0.43

-.38 -0.49 -0.48

-.48 -.54 -.48

.35

.37

.42

.54

_

.41

.61 -- .31

.49 .53

.45

.63 .43 .43

.56 .53

-

-.50 -- -.33

-.50 -- -.33

.40

|

<5 m

__

-

0.33

.35

_

--

--

.50

.45

--

~

-.47

-.48

.46

|

1

m

0.48

_.

-.43

.64

.65

.58

.64

.50

.54

.43

.67

.45

.87

.77

.50

.52

-.42

-42 f ^

.39

c

S

o 

m

._

-

0.66

.65

-

.56

.44

--

-

.44

.40

.39

.69

.66

.42

|

1

o

£

U

~

-0.53

-.60

.38

.37

.32

.44

_

--

--

.63

-.37

.63

.74

.39

.38

-.32

-.33

.51

£

n

.Q

O

u

0.47

-.35

.52

.55

.42

.62

.46

.47

.41

.35

-

.37

.73

.60

.47

.50

18 .jo

-.37

.34

£Q.

a.

o 

u

~

-0.54

-.57

.46

.43

--

.51

_

--

--

.71

-.41

.56

.70

.50

.46

.56

0>

o 8 w

(0

0.47 -0.35

-.41

-.35 -.41

.46

.47

.43

.42

.34

.51

.47

.37 .53 -0.41

-.39

.39

.68 .34

.48 .52

.44

.45

-.47

-.47

-.37

.41

£

g

1

-0.40

-.39

--

.47

.35

--

--

.56

-.48

.41

.50

.47

.42

.48

E

3

1

.Q

 5

0.39

--

.75

.75

.42

.66

.65

.45

.38

.65

~

.47

.73

.67

.71

.71

.52

0>

u

z

-0.3

.

.

-

.4

_

-

.

.

-.3

.

.

.

.4

.

.
Table 25. Correlation coefficients for 90th-percentile measurements of physical properties and element concentrations in water 

upper Illinois River Basin Continued

Element in streambed sediment

Physical property 

or element in water

Specific conductance

PH

Temperature

Dissolved oxygen

Hardness

Calcium, total

Calcium, dissolved

Magnesium, total

Magnesium, dissolved

Sodium, total

Sodium, dissolved

Potassium, total

Potassium, dissolved

Chlorine, dissolved

Solids, total suspended

Solids, volatile

E

3 

C

E

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Table 26. Correlation coefficients for concurrent measurements of physical properties and elements in water and streambed se

[Correlations were done with the concentrations less than the minimum reporting level (MRL) set to zero. Correlations not shown if majority of concentratio

--, correlations with p>0.10]

Major and TraceE!

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Element in streambed sediment

Physical property or 

element in water

Aluminum, total

Arsenic, total

Barium, total

Barium, dissolved

Boron, total

Boron, dissolved

Iron, total

Manganese, total

Manganese, dissolved

Phosphorus, total

Phosphorus, dissolved

Strontium, total

Strontium, dissolved

Discharge

Specific conductance

PH

Temperature

Dissolved oxygen

Hardness

Calcium, total

Calcium, dissolved

Magnesium, total

Magnesium, dissolved

Sodium, total

Sodium, dissolved

Potassium, total

Potassium, dissolved

Chlorine, dissolved

Solids, total suspended

Solids, volatile

Aluminum

-

0.48

-.48

-.53

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.34

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-.33

-.42

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-.46

-.68

-.66

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= -a E I O t 5 « E5" ^ ^_ 

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Chromium

0.75

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-.61

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Manganese Mercury

0.51

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0.39 -.48

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33

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-

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0.67

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0

JC

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0

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-.

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-.

-.
APPENDIXES
APPENDIX A. RESULTS OF CHEMICAL ANALYSES OF WATER, SEDIMENT, 

AND BIOTA

Results from the analysis of elements in water, sediment, and biota samples collected from 1987 through 1990 are shown 

here in detail. Included are Tukey box plots of the dissolved (fig. Al), total recoverable (fig. A2), and suspended-sediment 

data (fig. A3) by site. Concentrations of all elements in streambed sediment data for individual sites can be found in Colman 

and Sanzolone( 1991).

Results of analysis of elements in biota are presented in table Al. Concentrations of elements in streambed-sediment 

samples collected concurrently with the tissue samples are presented in tables A2 and A3. Loads and yields from total recoverable concentrations in water are presented in table A4. Trends in concentrations in water are presented in table A5.

158 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
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SITE NUMBER

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A2. Continued. Figure 

LITER PER MICROGRAMS IN MANGANESE, RECOVERABLE TOTAL 

c en ivj - 

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SITE NUMBER

Figure A2. Continued.
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NUMBER SIT 

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MICROGRAMS IN VANADIUM, RECOVERABLE TOTAL 

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SITE NUMBER

Figure A3. Concentrations of elements in suspended sediments in the upper Illinois River Basin, 1987-90 (see figure 5 for site 
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SITE NUMBER

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£ 90

UJ

1 80

UJ

Q 70

UJ

g 60

UJ

Q.

(/) 50

13

Z 40 

§ 30 5

< 20 5 100

'----

'-

'- 1 XXX ----

>< 1 Jo : VXX > X < X >><< -:-:

-_

o -1 ><><X

-

 n

to*i£

14 28 40 55

SITE

A

69 76 89

---:~

99

NUMBER

Figure A3. Continued.

M

CO
3 O

D O< M OCO

M" C\TT-~r-"

WVdO d3dSWVdOC 

jor andTrace Elements inWater, S

a w n ,400

I i

3 Z 1 ,200

a 

3 K^

of m

- s 1.000

00 in

<b 0)

0 a eoo

UJ

Q

Z 

111 a. eoo

CO

^_

5 400

o

z

N

200

0

o

o 

o

o

x o o '

X

I I X X | " " ' ' |

K I I -

I * I I I I

ii x ' '

14 28 40 55 69 76 89 99

SITE NUMBER

Figure A3. Continued.
Table A1. Element concentrations in biota from the upper Illinois River Basin, 1989-90

[Concentrations are in micrograms per gram dry weight, n, number of individuals per composite sample; length is in millimeters; weight is in grams; --, no dat

Site 

number 

(fig. 5)

2

2

6

9

9

11

14

14

24

25

27

28

38

38

38

38

38

40

40

40

45

45

45

46

46

52

52

53

53

58

63

66

66

66

66

69

69

76

78

80

Sample 

collection date

1989

--

--

~

July 24

July 31

July 31

__

July 25

July 25

July 25

_

July 25

July 25

July 25

August 2

August 2

August 2

August 2

August 4

~

August 4

July 28

August 1

August 1

August 3

--

July 29

August 1

July 27

~

-

1990

August 2

August 2

August 3

August 2

August 2

August 13

July 30

July 31

July 31

August 1

August 8

~

~

August 9

~

August 9

~

August 3

August 3

August 13

August 7

~

August 7

August 8

August 8

August 4

August 11

August 11

Organism

White sucker

Curly leaf pondweed

White sucker

White sucker

White sucker

Common carp

Asiatic clam

Common carp

Fat mucket/giant floater

Common carp

Fat mucket

Common carp 

Fingernail clam

Caddisflies

Crayfish

Common carp

Wild celery

Crayfish

Common carp

Goldfish

Crayfish

Water weed

Sago pondweed

Ashy physa snail

Eurasian watermilfoil

Crayfish

Goldfish

Common carp

Sago pondweed

Common carp

Common carp

Crayfish

Crayfish

Common carp

White sucker

Asiatic clam

Common carp

Common carp

White sucker

Elktoe

Length/weight

1989

../..

 /._

__/._

../._

../..

491/1,556

_ /

440/1,340

../__

../--

../--

._/_.

../..

._/__

-/--

../..

._/._

._/._

._/__

313/873

../--

 /._

._/._

__/__

__/._

../..

~/~

 /..

._/.-

436/1,464

.-/..

 /--

._/__

508/1,743

../..

../..

506/1,888

570/2,452

.-/-.

--/--

1990

272/207

_./._

416/804

355/487

324/373

_./--

../__

540/2,451

../__

450/1,362

_./--

501/1,586

__/__

__/._

 /--

333/665

--/--

../..

489/1,697

__/--

__/--

../._

../--

._/__

__/--

__/--

196/168

478/1,765

--/_.

476/1,793

464/1,458

--/.-

-_/~

-./__

264/196

../..

497/1,743

356/669

242/214

--/--

n

1989

«

~

9

14

4

~

._

--

30

37

289

9

4

__

10

12

6

28

5

3

~

-

1990

10

5

10

10

__

~

10

4

4

3

6

8

~

10

~

._

~

~

~

10

10

~

7

8

~

~

--

10

13

10

10

10

5

Percent moistur

1989

_

75.6

86.3

78.6

__

71.3

85.7

71.2

96.0

78.6

68.7

78.9

95.6

77.1

95.0

76.3

93.3

71.8

79.0

76.7

71.6

--

84.4

67.3

80.5

~

1990

79.1

94.4

78.4

76.4

77.5

~

72.9

88.3

73.7

88.5

73.8

~

73.2

~

72.4

~

92.5

73.3

71.3

~

73.3

76.6

~

~

77

84

73.7

73.6

80.9

86.1
IS) 

O>

2

"o"

0) 

Q.

i1

8

m

5T

i

1

5'

f

1

jf*

0)

3

a

DO1'

of

Table A1.

Site

number

(fig. 5)

80

80

81

81

89

93

93

94

94

97

97

99

Element concentrations in biota from the upper Illinois River Basin, 1989-90 Continued

Sample

collection date

1989

_

August 3

August 3

July 25

--

--

--

July 11

"""

1990

August 1 1

August 10

~

August 10

August 4

August 4

August 6

August 6

August 5

August 6

Organism

Three ridge

Common carp

Common carp

Crayfish

Common carp

Plain pocketbook

White sucker

Common carp

Common carp

Crayfish

Golden redhorse

Common carp

Length/weight

1989 1990

__/-- ../..

--/-- 519/1,790

499/2,965 --/--

_-/.- ._/._

556/2,258 470/1,402

../-- ../-

--/-- 266/206

--/-- 539/2,178

--/-- 468/1,393

../.. __/--

--/-- 270/213

--/-- 464/1,396

n Percent moistur

1989 1990 1989

6

10

9 -- 74.4

74.8

10 10 68.9

6

10

10

10

15 - 80.8

10

8

1990

83.2

73.6

~

72.6

87

78.6

72.3

73.9

72.5

75.9

§
Table A1. Element concentrations in biota from the upper Illinois River Basin, 1989-90 Continued

(D

Site 

number

(fig. 5)

2

2

6

9

9

11

14

14

24

25

27

28

38

38

38

38

38

40

40

40

45

45

45

46

46

52

52

53

53

58

63

66

66

66

66

69

69

76

78

80

Organism

White sucker

Curly leaf pondweed

White sucker

White sucker

White sucker

Common carp

Asiatic clam

Common carp

Fat mucket/giant floater

Common carp

Fat mucket

Common carp

Fingernail clam

Caddisflies

Crayfish

Common carp

Wild celery

Crayfish

Common carp

Goldfish

Crayfish

Water weed

Sago pondweed

Ashy physa snail

Eurasian watermilfoil

Crayfish

Goldfish

Common carp

Sago pondweed

Common carp

Common carp

Crayfish

Crayfish

Common carp

White sucker

Asiatic clam

Common carp

Common carp

White sucker

Elktoe

Barium

1989 1990

<0.1

24.4

<.l

<.l

<.l

0.1

6.4

.3 <.l

- 198

<.l

-- 585

<.l

4.9

21.8

24

<.l

32.3

23.1

<.l

<.l

32.6

38.7

-- 38.9

12.3

15.6

27.5

<.l

<.l

47.3

.2 <.l

.1

40.9

34.6

<.l

<.l

4.3 5

.2 <.l

.2 <.l

<.l

-- 124

Beryllium Boron

1989 1990 1989

<0.1

<. 1

<.l

<.l

<.l

<0. 1 - <2

<.l -- <2

<.l <.l <2

<. 1

<.l

<.l

<.l

<.l -- 3

<.l -- 6

<.l -- 3

<.l

<.l -- 17

<.l -- 2

<. 1

<.l -- <2

<.l -- 2

<.l -- 18

<.l

<.l - <2

<.l - 15

<.l -- 120

<. 1

<.l

<.l -- 343

<.l <.l <2

<.l

<.l -- 5.9

<.l - 6

<.l - <2

<.l

<.l <.l <2

<.l <.l <2

<.l <.l <2

<. 1

<. 1

1990

<2

13

<2

<2

<2

<2

<2

<2

<2

<2

~

<2

«

<2

~

__

205

~

_

<2

<2

<2

<2

<2

<2

<2

<2

<3

<2

Cad- Chromium mium Copper

1989

-

1.2

.30

.75

._

.30

.2

.2

_.

3.5

<.2

~

3.1

<.2

1.5

~

5.9

8.6

<.3

1.3

1.2

__

<.2

<.2

1.2

.4

.93

9.5

-

1990 1989

<0.3

.5

<.3

<.3

<.3

-- <1

<1

1.8 <1

.96

3.8

2.2

44.8

<1

5.4

2

2.1

2

2

4.6

-- <1

1

3

.7

6

11

1

.5

.6

10

2.8 <1

3

2

2

<1

.5

.6 <1

1.9 <1

2.4 <1

<.4

1.8

1990 1989

<1

1

<1

<1

<1

77.3

12

<1 88.1

<1

<1

1

<1

22

27.2

-- 152

<1

27.5

81.5

<1

46.9

-- 185

48.6

3

- 209

38.4

115

<1

<1

20

<1 24.1

<1

-- 165

-- 170

72.9

<1

2 32.9

<1 74.9

<1 122

<1

2

1990

100

3.8

65.8

68.6

45.9

__

56.2

8.8

146

11

116

115

65.6

..

17

_

34.1

18

16

153

153

38.6

91.8

103

100

7

Iro

1989

..

~

732

110

651

_.

293

2,370

402

__

843

573

680

230

1,000

668

1,090

313

2,510

289

508

395

629

--

143

669

432

--
10 

00

S

f

o>

a

H

8

m

<o

<o

n?w5'

i

8

§<o

o>

3

a

03

0

ST

Table A1 . Element concentrations in biota from the upper Illinois River Basin, 1989-90 Continued

Site

number

(fig. 5)

80

80

81

81

89

93

93

94

94

97

97

99

Beryl- Cad- ChroBarium Hum Boron mium mium Copper Iro

Organism

Three ridge

Common carp

Common carp

Crayfish

Common carp

Plain pocketbook

White sucker

Common carp

Common carp

Crayfish

Golden redhorse

Common carp

1989 1990 1989 1990 1989 1990 1989 1990 1989 1990 1989

72.2 -- <0.1 - <2 -- <0.3 -- 2

.1 -- <.l -- <2 -- 1.5 -- <1

<0.1 -- <0.1 -- <2 -- 0.72 -- <1 -- 62.3

89.6 -- <.l - 2 - <.2 -- 2 -- 54.9

<.l <.l <.l <.l <2 <2 .84 .89 <1 <1 66.1

-- 203 - <.l -- <2 -- .8 -- 2

.1 -- <.l -- <2 -- .5 -- <1

<.l -- <.l -- <2 -- 4 -- <1

<.l -- <.l -- <2 - 3.7 -- <1

129 -- <.l -- <2 - .30 - 2 - 76.4

<.l -- <.l - <2 -- <.3 -- <1

.48 - <.l -- <2 -- 18 - <1

1990 1989

4.1

124

-- 609

320

61 1,020

4.3

168

179

130

425

25

110
Table A1. Element concentrations in biota from the upper Illinois River Basin, 1989-90 Continued

H

cr

(D

*J

to

to

Site 

number

(fig. 5)

2

2

6

9

9

11

14

14

24

25

27

28

38

38

38

38

38

40

40

40

45

45

45

46

46

52

52

53

53

58

63

66

66

66

66

69

69

76

78

80

Mercury

Organism

White sucker

Curly leaf pondweed

White sucker

White sucker

White sucker

Common carp

Asiatic clam

Common carp

Fat mucket/giant floater

Common carp

Fat mucket

Common carp

Fingernail clam

Caddisflies

Crayfish

Common carp

Wild celery

Crayfish

Common carp

Goldfish

Crayfish

Water weed

Sago pondweed

Ashy physa snail

Eurasian watermilfoil

Crayfish

Goldfish

Common carp

Sago pondweed

Common carp

Common carp

Crayfish

Crayfish

Common carp

White sucker

Asiatic clam

Common carp

Common carp

White sucker

Elktoe

1989

_.

-

0.22

.09

.12

«

_

.03

.14

.12

._

.04

.07

.14

.15

.1

-

.08

.07

.1

.09

.06

.05

.06

.3

.10

.19

.17

-

1990

0.110

.005

.09

.11

.088

__

.14

.097

.15

.085

.33

-

.24

.13

..

.019

--

..

.093

.071

.061

.410

.330

.097

.29

.098

.548

.078

Molybdenum

1989 1990

1

2

<1

<1

-- <1

<1

<1

<1 1

<1

1

-- <1

<1

<1

3

<1

- <1

2

<1

1

<1

<1

2

- 17

<1

<1

<1

<1

1

4.5 -

<1 1

2

<1

<1

<1

1

<1 1

<1 1

2 <1

<1

- <1

Nickel

1989

-

<2

<2

<2

~

_

<2

7.6

3

30

2

<2

2

36

-

28

17

<2

-

6.7

<2

..

3

3

<2

2

<2

<2

--

1990

<2

2

<2

<2

<2

<2

<2

<2

<2

<2

<2

~

<2

..

11

__

<2

<2

~

<2

<2

~

<2

5

<2

<2

<2

7

Lead

1989

..

~

<4

<5

<4

~

_

-

<5

9

<4

_.

7

<4

<4

<4

8

--

9

9

<4

22

<4

<4

<4

<4

~

<4

<4

<4

--

1990

<5

<4

<5

<5

<5

..

<4

<5

<5

<5

<5

-

<5

<4

~

_.

5

_.

<5

<5

<4

<5

--

._

<5

<5

<5

<5

<5

<5

Selenium

1989

..

--

4.4

1.7

4.2

_

.5

2

1.2

.4

<51.4

«

4.7

2

.6

--

1.6

.5

1.1

.7

3.9

1.6

1.4

6.3

--

3

3.9

6.1

--

1990

5.2

.3

4.7

5

4.8

6.3

2.6

7.4

2.6

5.7

4.5

--

7.2

__

.5

4.9

5.4

7.3

7.9

5.2

2.9

5.3

6.2

4.6

1.8

Silver

1989

~

<2

<2

<2

~

_

<2

<2

<2

<2

<2

<2

<2

<2

~

15

<2

<2

~

<2

<2

<2

<2

<2

--

<2

<2

3

--

1990

<2

<2

<2

<2

<2

<2

<2

<2

<2

<2

~

<2

~

<2

..

<2

_.

<2

<2

<2

<2

~

2

<2

<2

<2

<2

<2

Stron

tium

1989

~

--

0.2

2.4

.4

~

~

_

582

16.7

567

__

94.7

440

~

.5

221

56.2

-

167

37.7

160

47.3

1.1

339

334

.3

9.6

1.8

.7

--

<

2
ro 

ro

o

S

o> "o"

so

Q.

H

8

s

m

A

i

3

W

5'

i?

.71

§.

1

J*

o>

3

Q.

03

aof

Table A1 . Element concentrations in biota from the upper Illinois River Basin, 1989-90 Continued

Site

number

(fig. 5)

80

80

81

81

89

93

93

94

94

97

97

99

Organism

Three ridge

Common carp

Common carp

Crayfish

Common carp

Plain pocketbook

White sucker

Common carp

Common carp

Crayfish

Golden redhorse

Common carp

Mercury

1989 1990

-- 0.094

.30

.24 --

.04 -

.27 .25

.083

.34

.36

.24

.08 --

.11

.23

Molybdenum

1989 1990

<1

2

<1

<1

<1 1

1

1

1

1

<1

-- <1

1

Nickel

1989 1990

- <2

-- <2

<2

4

<2 <2

8.9

-- <2

-- <2

-- <2

<2

-- <2

-- <2

Lead

1989

<4

<4

<4

<4

._

--

1990

<5

<4

«

<4

<6

<5

<5

<5

<5

<5

Selenium

1989 1990

-- 1.9

-- 7.2

3.7

1.5

4 4.3

-- 1.9

-- 5.5

- 7.6

-- 7.4

2

-- 5.5

-- 5.1

Stron

Silver tium 

1989 1990 1989

<2

5

<2 -- 0.1

<2 -- 114

<2 <2 .5

<2

<2

<2

<2

<2 -- 149

<2

<2
Table A2. Major element concentrations in streambed sediments in the upper Illinois River Basin, August 1990

[All concentrations are in percent]

Site number 

(fig. 5)

2

6

9

14

24

25

27

28

38

40

45

52

53

58

63

66

69

76

89

93

94

97

99

Date

Aug. 2, 1990

Aug. 3, 1990

Aug. 2, 1990

Aug. 13, 1990

July 30, 1990

July 30, 1990

July 31, 1990

Aug. 1, 1990

Aug. 8, 1990

Aug. 9, 1990

Aug. 9, 1990

Aug. 3, 1990

Aug. 3, 1990

Aug. 13, 1990

Aug. 7, 1990

Aug. 7, 1990

Aug. 8, 1990

Aug. 4, 1990

Aug. 10, 1990

Aug. 4, 1990

Aug. 6, 1990

Aug. 5, 1990

Aug. 6, 1990

Aluminum

3.5

4.7

4.1

5.0

6.6

6.2

6.2

6.6

6.2

5.3

6.2

5.9

6.1

6.0

5.5

5.2

4.9

5.9

3.8

4.5

4.7

4.5

4.3

Calcium

4.2

2.8

4.4

3.9

1.9

2.3

3.1

2.9

4.2

5.9

4.6

4.8

4.7

5.0

4.0

4.5

6.6

4.4

14

5.8

6.4

6.4

9.4

Iron

7.2

7.4

9.1

5.3

3.2

2.9

3.1

3.4

3.5

3.2

3.3

3.3

3.5

3.7

3.2

3.1

2.7

3.5

2.3

2.8

2.4

2.1

2.1

Potassium

1.2

1.4

1.5

1.7

2.7

2.9

2.6

2.5

2.6

2.3

2.6

2.5

2.5

2.4

2.1

2.1

1.9

2.3

1.3

1.5

1.6

1.7

1.6

Magnesium

0.82

1.1

1.2

1.4

1.5

1.7

1.8

1.8

2.7

3.3

2.9

2.6

2.6

2.9

2.3

2.4

2.5

2.2

2.1

1.4

1.7

2.1

2

Sodium

0.38

.58

.47

.57

.56

.56

.5

.48

.51

.5

.47

.52

.47

.39

.61

.63

.61

.52

.36

.79

.65

.75

.6

Phosphorus

0.19

.17

.27

.15

.07

.06

.08

.90

.22

.2

.16

.22

.26

.35

.19

.17

.15

.23

.12

.11

.11

.07

.1

Table A2 221
o

O)

O)

"55

3 

O)

3

c"

(0

CD

Vif

CO 'o

_c

Q. 

Q.

0)

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222 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90

[Sites included are those with continuous discharge data and more than 30 observations. Sites with more than 90 percent of the observations less than the det

Loads were calculated twice, once with censored values set to zero and once with censored values set to the detection limit. --, calculations resulted in the sam

no or few censored values were present; >, greater than]

Load (tons per year)

Site 

number

(fig. 5)

Number of 

observations

Censored 

values set to 

zero

Censored 

values set to 

detection limit

Standard deviation of mean annual load

Censored 

valuses set to 

zero

Censored 

values set to 

detection limit

14

20

22

28

31

32

34

39

40

45

50

55

62

69

76

86

89

99

14

28

31

40

45

55

69

76

89

99

Total recoverable aluminum

47

32

31

50

41

31

31

31

43

31

32

67

31

72

57

31

72

45

46

47

41

43

31

67

69

56

70

45

3,850

652

1,190

7,270

17,200

46.0

327

155

985

729

369

1,050

39.7

I,620

II,700

144

8,190

2,980

4.81

3.28

10.0

1.54

.16

4.27

.46

17.7

41.2

2.71

2,710

3,800

305

368

1,220

77.0

9,470

1,570

221

86.3

75.6

90.5

231

63.0

58.5

172

57.5

275

376

52.3

54.9

169

66.4

706

117

610

Total recoverable arsenic

4.62

2.49

8.78

.14

_

.52

18.2

22.5

2.69

52.1

126

116

39.4

52.9

38.2

85.1

50.4

48.3

92.7

95.4

103

71.4

81.0

81.0

88.3

42.2

85.7

34.8

46.5

50.6

26.0

42.5

33.7

21.7

31.6
!o Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 C

s

*o'

D)

a.

8

m

(D

(D

W

5"

s(D

^P

a

3

(D

3

0)

a

CD5'

sr

to

T

o

Load (tons per year)

Site 

number 

(fig. 5)

Number of 

observations

Censored 

values set to 

zero

Censored 

values set to 

detection limit

Standard deviation of mean annual load

Censored 

valuses set to 

zero

Censored 

values set to 

detection limit

Total recoverable barium

14

20

22

28

31

32

34

39

40

45

50

55

60

62

69

76

86

89

99

47

32

31

50

31

31

31

31

43

31

32

67

31

31

72

57

31

71

45

135

33.9

15.6

108

301

3.03

11.9

1.03

35.1

4.74

4.96

62.8

3.57

3.01

25.4

457

6.93

669

148

304

_

13.6

29.4

-

_

61.5

_

_

-

16.2

7.72

20.8

20.5

135

23.6

155

18.5

116

38.3

33.1

79.9

46.6

38.8

23.1

26.4

20.5

16.0

24.2

-

34.3

_

38.7

24.5

-

_

32.5

_

-

Total recoverable boron

14

20

22

28

31

32

34

39

40

45

50

55

60

62

69

47

32

31

50

31

31

31

31

43

31

32

67

31

31

72

34.6

20.8

7.60

79.3

289

10.8

42.4

8.44

125

13.5

20.9

428

12.0

8.74

68.3

119

27.4

14.8

87.9

297

7.43

_.

-

..

_.

61.6

7,500

1,160

886

1,930

2,720

804

15.3

31.8

18.9

21.5

23.0

11.4

22.8

23.4

118

13.7

22.3

23.0

21.6

21.5

48.2

--

..

__

16.7
Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 C

Load (tons per year)

Site 

number 

(fig. 5)

Number of 

observations

Censored 

values set to 

zero

Censored 

values set to 

detection limit

Standard deviation of mean annual load

Censored 

valuses set to 

zero

Censored 

values set to 

detection limit

Total recoverable boron Continued

76

86

89

99

57

31

72

45

1,090

.32

40.9

98.8

_

6.15

668

134

22.3

1,110

757

1,570

_

7.59

14.4

20.7

Total recoverable cadmium

14

28

39

40

45

55

69

76

89

99

47

49

31

43

31

67

72

57

72

45

.55

.28

.01

.39

.08

3.24

.09

4.95

4.78

.45

1.40

.57

.07

.35

3.65

.37

9.99

301

.91

81.1

50.8

155

63.8

193

146

71.2

78.6

40.2

68.6

132

72.7

15.5

21.5

62.6

146

99.3

116

87.8

Total recoverable chromium

14

20

22

28

31

32

34

39

40

45

50

55

60

62

69

76

86

89

99

47

32

31

50

41

31

31

31

43

31

32

67

31

31

72

56

31

72

45

36.0

1.04

1.36

19.3

176

.18

2.08

.62

10.3

.98

2.71

30.0

.73

1.46

5.68

145

.29

6.79

51.5

18.8

2.92

2.12

18.3

81.0

.40

2.16

.25

7.53

.74

2.79

30.4

.73

.27

3.16

105

.70

47.4

31.4

1,120

467

1,720

1,290

1,810

800

815

760

1,150

1,050

2,870

422

2,060

545

1,150

1,100

835

732

2,060

58.8

17.7

58.9

71.5

96.0

21.1

33.3

58.3

51.9

28.9

129

52.5

77.8

40.0

51.5

59.1

20.4

60.9

108
Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 

Major an<

u.

3

o

(D

m

(D

»

1

5'

D)

<D

1

3

§r*

D)

CD5'

sr

IL

5

£

°

Load (tons per year)

Site 

number 

(fig. 5)

Number of 

observations

Censored 

values set to 

zero

Censored 

values set to 

detection limit

Standard deviation of mean annual load

Censored 

valuses set to 

zero

Censored 

values set to 

detection limit

Total recoverable cobalt

20

34

40

45

50

55

32

31

43

31

32

67

0.24

.13

1.14

.08

.11

.72

2.81

1.73

4.35

.59

.65

13.3

169

207

137

210

197

80.3

14.0

22.0

44.8

26.5

19.3

3.14

Total recoverable copper

14

20

22

28

31

32

34

39

40

45

50

55

60

62

69

76

86

89

99

47

32

31

50

41

31

31

31

43

31

32

67

31

31

72

57

31

72

45

8.98

1.00

.65

19.4

19.6

.14

1.54

.60

21.3

216

2.67

32.1

.09

.88

7.69

186

.10

53.2

9.97

16.0

2.81

1.77

13.8

31.5

.41

2.22

.50

10.7

1.78

1.16

24.5

.54

.32

3.63

119

.62

247

12.9

357

430

254

536

311

746

803

231

610

695

1,220

580

187

412

789

1,340

196

339

493

41.0

15.5

28.9

45.8

25.4

35.7

49.6

74.9

59.5

40.2

41.5

51.2

23.8

27.3

45.2

71.3

10.3

39.4

30.2

Total recoverable iron

14

20

22

28

31

47

32

31

50

41

4,960

737

1,270

9,450

16,400

_

7,920

-

55.0

67.0

72.5

296

71.7

_

99.4

--
Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 C

Site 

number

(fig. 5)

Load (tons per year) Standard deviation of mean annual load

Number of 

observations

Censored

values set to

zero

Censored 

values set to 

detection limit

Censored

valuses set to

zero

Censored

values set to

detection limit

32

34

39

40

45

50

55

60

62

69

76

86

89

99

31

31

31

43

31

32

67

31

31

72

57

31

72

45

59.1

501

55.5

1,480

879

456

1,610

284

66.5

1,700

17,300

103

36,400

2,210

Total recoverable iron Continued

52.9

42.9

58.5

53.6

294 373

487

1,740

1,810

30,800

395

171

70.8

54.1

220

49.6

56.9

120

77.6

66.1

75.0

56.4

91.6

34.6

Total recoverable lead

14

28

32

39

40

45

50

55

60

69

76

99

47

50

31

31

43

31

32

67

31

71

57

44

1.97

3.46

.03

.27

26.3

13.0

2.19

44.5

.27

4.33

117

4.40

23.0

15.9

4.13

1.05

9.83

9.09

5.18

50.1

3.30

6.65

125

20.7

185

328

218

463

304

332

1,030

371

259

200

919

247

76.1

63.3

59.1

77.9

37.8

73.2

66.2

63.5

65.1

93.5

68.6

59.0

Total recoverable manganese

14

20

22

28

31

47

32

31

50

41

309

33.3

24.4

158

644

336

578

141

36.8

62.2

64.4

145

32.0

64.4
ro 

ro Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 

S

u"o"

u

3

Q.

2

S

m

(D

»

7

5"

u

»

^>

Q.

i

3

J*

U

Q.

m o'

Load (tons per year) Standard deviation of mean annual load

Site

number

(fig. 5)

32

34

39

40

45

50

55

60

62

69

76

86

89

99

Number of

observations

31

31

31

43

31

32

67

31

31

72

57

31

72

45

Censored

values set to

zero

6.43

25.0

3.20

65.9

12.0

14.6

138

7.01

3.03

42.7

801

10.2

1,080

152

Censored Censored Censored

values set to valuses set to values set to

detection limit zero detection limit

Total recoverable manganese Continued

59.3

27.0

53.2

32.3

41.6

31.7

22.7

39.5

36.7

49.9

29.8

35.1

26.4

48.8

55

69

47

43

.37 

.05

Total recoverable mercury

26.2

58.8

Total recoverable nickel

14

20

22

28

31

32

34

39

40

45

50

55

60

62

69

47

32

31

50

41

31

31

31

43

31

32

67

31

31

72

7.56

2.67

1.58

8.98

52.0

0.13

1.36

.52

4.91

.34

2.62

53.9

.14

.29

1.83

14.3

3.57

2.29

12.9

48.1

0.46

2.30

.31

6.74

.81

1.70

52.3

.56

.40

2.51

644

1,100

878

1,550

1,200

422

809

1,070

981

1,550

2,470

86.8

630

1,360

1,240

28.2

30.6

46.7

51.5

51.1

30.7

40.1

65.6

53.4

43.5

75.3

51.2

43.9

62.3

43.9
Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 C

Site

number 

(fig-5)

Load (tons per year) Standard deviation of mean annual load

Number of 

observations

Censored

values set to

zero

Censored 

values set to 

detection limit

Censored

valuses set to

zero

Censored 

values set to 

detection limit

Total recoverable nickel Continued

76

86

89

99

20

45

57

31

72

45

32

31

141

.46

122

10.1

.34 

.04

112

.94

1370

15.3

534

1,260

283

1,100

Total recoverable silver

1.86 

.34

189

164

57.6

54.6

34.3

56.1

19.7

20.3

Total recoverable strontium

14

20

22

28

31

32

34

39

40

45

50

55

60

62

76

86

89

99

47

32

31

50

41

31

31

31

43

31

32

67

31

31

57

31

72

45

290

114

38.3

281

748

49.1

132

17.9

292

33.5

29.0

20.5

11.7

2,020

20.0

9880

719

6.47

7.60

17.8

16.0

19.0

14.8

54.1

14.3

34.7

17.8

17.2

16.4

18.2

17.3

9.20

8.58

17.7

22.0

Total recoverable vanadium

14

20

22

28

31

47

32

31

50

41

1.69

I.13 

.69

7.28

II.3

12.3

2.75

1.77

10.7

32.4

162

334

319

601

339

18.4

14.4

31.5

28.4

30.9
Table A4. Calculated loads and yields for total recoverable elements from 26 sites in the upper Illinois River Basin, 1987-90 C

^ Load (tons per year)

0) "o

0)

Q.

1(D

m

ID

o

15'

1»

^)

1

3

f

0)

Q. 

03

o

$~-i 

*

1°

O

Site 

number

(fig. 5)

Number of 

observations

Censored 

values set to 

zero

Censored 

values set to 

detection limit

Standard deviation of mean annual load

Censored 

valuses set to 

zero

Censored 

values set to 

detection limit

Total recoverable vanadium Continued

32

34

40

45

50

62

69

76

86

31

31

43

31

32

31

72

57

31

0.09

.17

.51

.04

.68

.04

1.63

12.1

.14

0.35

1.68

3.49

.51

.75

.22

2.25

56.0

.62

568

224

169

155

229

212

273

260

143

20.7

9.72

5.37

16.1

24.4

15.9

24.2

22.2

16.8

Total recoverable zinc

31

33

38

39

40

50

55

62

69

76

41

30

30

31

43

32

67

31

72

57

56.1

1.98

72.4

11.8

55.3

.87

394

.68

50.1

491

299

17.1

2.77

68.7

11.6

301

3.25

31.6

910

1,070

1,300

1,880

12,100

>20,000

725

5,230

1,390

2,270

8,740

34.4

56.7

~

52.0

43.3

32.9

31.6

50.7

52.0

46.8
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90

[Censored data treatment: 0 denotes censored values set to zero; D denotes censored values set to the detection limit; , all data were above the detection limit

Site

number 

(fig- 5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1

Per

m

Per year pe

14

20

22

28

31

31

32

33

34

35

38

39

40

43

45

49

50

54

56

57

60

62

64

65

67

69

69

72

74

76

84

86

88

89

90

D

72

62

61

72

61

61

61

57

62

62

62

62

65

62

63

64

63

62

59

64

58

58

57

59

61

70

70

59

60

63

63

62

60

69

56

Total recoverable aluminum (micrograms per liter)

0.065

-.01

-.03

.038

.03

.015

-.11

-.16

-.09

.041

.099

.07

.084

-.25

.027

.15

.091

.13

-.18

.087

.046

.14

.097

.26

.16

-.06

-.06

.12

-.09

.038

-.13

-.06

.046

-.01

-.03

0.56

.95

.85

.75

.85

.95

.36

.23

.47

.77

.43

.58

.48

.030

.86

.21

.46

.31

.16

.47

.75

.26

.47

.035

.19

.58

.58

.36

.48

.78

.29

.66

.74

1

.88

4.7

-2

-4.1

14

2.5

2.5

-17

-20

-11

7.2

36

28

32

-60

5.3

49

30

23

-11

8.8

14

31

26

57

35

-7

-6.5

18

-15

15

-7.4

-5.4

1.3

-.38

-4

-

-

-

-

-

1

-

-

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site 

number 

(fig. 5)

Censored

data 

treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

0)

91

91

92

92

93

93

96

96

99

99

50

50

14

14

28

28

31

31

35

35

38

38

40

40

45

45

49

49

54

54

56

56

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D 

0 

D 

0

D 

0 

D 

0 

D

13

13

13

13

11

11

13

13

13

13

13

13

13

13

11

11

13

13

13

13

59

59

59

59

60

60

61

61

69

69

48

48

125

125

47

47

82

82

112

112

113

113

32

32

112

112

74

74

87

87

116

116

Total recoverable aluminum (micrograms per liter) Continued

-0.21

-.21

-.15

-.15

-.05

-.05 

.12 

.12

-.14

-.14

0.084

.084

.25 

.25 

.74

.75 

.32 

.32 

.22 

.22

Dissolved aluminum (micrograms per liter)

.16 

.11

.26

.45

Total recoverable arsenic (micrograms per liter)

0.12 

.28 

.37 

.18 

.60

.41

.020

.015

.46

.20

.20

.12

.16

.20

-.05

-.06

-.32

-.34

-.09

-.14

.13

.033

-.07

-.12

-.19

-.16

-.01

-.02

.12

.046

.0033

.072

.23

.11

.58

.50

.000010

.0000032

.20

.041

.61

1

.33

.068

.039

.074

.89

.79

.087

.50

1

.74 

I

.54 

.15 

.080

.13 

.92 

.84 

.41 

.71

-16

-11

-38

-36

-18

-16 

20 

16

-21

-16

-

-

-

-

-

-

-

-

0

0

0

0

0

0

-.25

-.25

0

0

.045

0

0

0

0

0

0

0

0

0

-

-
Table AS. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Site

number 

(fig. 5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

Total recoverable arsenic (micrograms per liter) Continued

57

57

69

69

76

76

84

84

89

89

92

92

99

99

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D 

0 

D

9

9

13

13

11

11

13

13

13

13

13

13

13

13

76

76

47

47

79

79

117

117

47

47

109

109

124

124

-0.18

-.18

.12

-.03

-.19

-.23

-.11

-.15 

.11 

.013

.035

-.02 

.059 

.008

0.036

.041

.34

.88

.027

.0067

.11

.031

.43

1

.63 

.78 

.39 

.91

0.48

.88

.086

.038 

.36 

.19 

.65

1

.73 

.84 

.64 

.95

Dissolved arsenic (micrograms per liter)

14

14

69

69

76

89

89

99

99

0 

D 

0 

D

0 

D 

0 

D

38

38

38

38

35

36

36

35

35

-.05

.071

-.02

-.12

-.03

-.03

.053

.22

.083

.82

.47

1

.40

1

1

.82

.23

.67

Total recoverable barium (micrograms per liter)

a> 

cr

14

20

22

28

31

31

32

33

34

34

0 

D

0 

D

10

11

11

10

10

10

10

10

10

10

93

83

83

89

89

89

82

82

87

87

.19

.091

.019

-.04 

.01

.031

-.14

-.18

-.07

-.05

.026

.35

.87

.69

.94

.76

.1

.055

.49

.62

.070

.31

.87

.69

.95

.79 

.17 

.13 

.67

.73

.5 

.4 

0

-.2 

0

.11

-.90

-1

-.33

-.21
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Site 

number 

(fig. 5)

Slope

Censored

data 

treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

35

38

39

40

43

43

45

49

50

54

56

57

60

62

64

65

67

69

72

74

76

84

86

88

89

90

91

92

93

96

99

10

10

10

10

10

10

10

10

10

11

10

9

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

89

86

84

86

86

86

88

73

85

84

80

77

82

78

81

75

81

90

80

82

87

86

88

80

92

80

80

80

84

83

94

Total recoverable barium (micrograms per liter) Continued

0.20

.0062

.48

.028

.85

.66

.96

.95

.018

.077

.0073

.41

.0026

.012

.54

.0059

.012

.20

.46

.077

.079

.87

.37

.82

.91

.039

.074

.56

.099

.013

-0.18

-.47

-.08

-.26

.027

.062

-.01

-.01

-.31

-.21

-.34

-.09

-.09

-.68

-.5

-.09

-.37

-.28

-.17

-.09

-.19

-.15

-.02

.14

.034

-.02

-.22

-.22

-.06

-.17

0.049

.00000024

.39

.0051

.79

.51

.94

.96

.0009

.023

.0003

.37

.34

0

.00000013

.39

.0001

.0012

.071

.34

.034

.10

.88

.16

.71

.89

.021

.024

.56

.074

-.34 .000063

-0.5

-4

-.33

-1.5

.33

.5

0

0

-2

-1

-1.4

-.6

-.5

-16

-6.4

-.58

-2.0

-2

-.85

-.65

-.93

-.41

0

.6

.083

-.2

-3.2

-1.3

-.4

-.62

-

-

-

-

-

-

-

-

-1

-

-

-

-

-

-

-

-

-

-2.5 -
SE2

VO tO 45- 45- ON : : DO i o o o o o 

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to

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.L.L L 

CO Cft O 45. 

ON to 

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II II 

to to 1 i to 

NJ -J <-' O VO 

Cft

ON co 

to vo 

Cft Cft 45. CO 

ON Cft > co 

ON ON ON ON ON O tO £. Cft -J 

i i i i i i i i i i O O O O O 

ON ON ON ON ON 

CO J». h- tO ^J 1 1 1 1 1 

CO ON OO " * VO o §

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45. 45. 00 45. ON O O Cft h to 

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-J -J 

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Cft Cft K- tO VO 

Cft 45. 

ON *> O O ON 

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to 1 1 1 CO tO CO CO i O VO CO * 

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f^t «*J f^°l «*J f^*l f^*l f^*l f^*l f^*l f^*l 

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O 0 till § *i_i OCO^)> '45. > tO > i * i ~

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 * cotoi-'Loo LoLovovOh O OCft-~JvO^ tOtOCftCACft 

o*3

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h-h-o 1 0 1 1 

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-^J 45. CO * t CO CO 

> tO tO 1 O i > 

-- 1 Cft-~J45.O Cft-J OOOO 

oo ON vo co 

p^ ^fr p^ pv p^ CO CO CO 

45. i O ON to OOOO 

45.45.45.ON45. CO(O45. 

-~J O tO 00 tO O VO i 1 1 

m c 3 

^ 3 <P 

«*

O =T S

O) w a -* 

sf

II

X? ^ g 0 w O n n 

Si

O

z ST c » 3 i 

Ifo O =* 3 «HD)

T?

D) CO

> o c u 

Is"Lo. ~*

 o0^

wo

W 3. 

03^

"5 

O 0 -i 2 Sh < 

3. o 3

-3, S

(0

s li 

5' Q. ^ 

3 

5" <o 3 03 r

(O0 1 s

«r

(D

pi H

CDD

0.

S" w

CDW

5?D

0. 3

(D

Q. DOOO

(D

D^ S5" DW4 o

(D

(D3

(D

5T

5' wI

3 $

00

(D"*

D"

(DC

T3

T3

CD

5' ow'

33

(D

CD

03wp

CD

^J

00

COIoo

5' c

(D

Q.
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Site 

number

(fig- 5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

84

86

88

89

90

91

92

93

96

99

10

10

10

10

6

10

10

10

10

10

80

69

66

70

39

66

76

60

68

86

Dissolved barium (micrograms per liter) Continued

0.19 

.37 

.64 

.67

.17 

.96 

.78 

.48 

.44

-0.14

.091

.081

.066

-.1

-.13

-.01

.032

-.07

-.08

0.15

.41

.49

.56

.62

.24

.96

.84

.56

.42

-0.33

.18

.33

.2

-.79

-1.5

0

.1

-.25

-.5

-

-

-

Total recoverable boron (micrograms per liter)

14

14

20

20

22

22

28

28

31

31

32

32

33

34

35

38

39

40

43

43

45

49

50

54

56

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D

0 

D

D

13

13

13

13

13

13

13

13

10

10

13

13

10

13

12

13

12

13

13

13

13

11

12

13

13

101

101

84

84

85

85

94

94

89

89

89

89

82

93

90

111

104

95

94

94

91

74

102

107

102

-.35

-.04

-.26

.058

-.21

-.11

-.23

-.1

.054

.207

-.14

-.13

.02

-.02

.109

-.25

-.12

-.17

-.15

-.15

-.06

-.16

-.48

-.33

-.56

.0000089

.66

.004

.54

.021

.22

.0052

.25

.56

.018

.12

.14

.86

.81

.23

.0012

.13

.046

.077

.077

.52

.12

.0000000043

.000027

0

.023

.82

.0031

.57

.056

.33

.0097

.29

.67

.15

.26 

.28 

.85 

.83 

.35

.011

.23 

.069

.23 

.23

.61

.22

.0013

.0090

.0012

-5

0

-4

0

-4.3

-1

-3.6

0

0

1

-2.8

_2

1.4

-1.3

4.6

-19

-13

-9.6

-2.5

-2.4

-.88

-1.7

-39

-7.5

-13

-1

-

-

-

-

-

-

-

-

-

-

-

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Site 

number

(fig- 5)

Slope

Censored

data 

treatment

Years of 

record

Number of 

observations Tau p-vaiue

Adusted 

p-value1 Per year

Per

m

pe

57

60

62

64

65

67

69

69

72

72

74

74

76

84

84

89

89

90

90

91

91

92

92

99

99

20

22

22

28

31

0 

D 

0 

D

0 

D

0 

D

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D

9

11

12

10

13

13

13

13

10

10

13

13

10

13

13

12

12

13

13

10

10

13

13

13

13

13

13

7

10

10

7

10

Total recoverable boron (micrograms per liter) Continued

77

84

96

84

103

111

118

118

80

80

88

87

90

90

83

83

101

101

80

80

87

87

87

87

96

96

56

59

59

63

75

-0.28

-.07

-.23

-.1

-.21

-.25

-.16

-.16

-.26

-.1

-.08

-.08

-.2

-.39

-.15

-.03

.13

-.11

.031

-.21

-.07

-.18

-.13

-.08

-.04

0

.058

0.0043

.45 0.32

.0075

.30

.0093

.001

.026

.028

.0054

.31

.41

.41

.031

.0000022

.082

.77

.16

.19

.72

.030

.46

.053

.16

.38

.66

1 1

.51

.024

.36

.023

.0087

.038

.038

.046

.52

.53

.53

.088

.0037

.24

.86

.44

.44

.85

.17

.60

.30

.45

.55

.76

.61

Dissolved boron (micrograms per liter)

-.06

-.15

-.14

-.17

.01

.64

.22

.25

.12

.96

_

.27

.30

.96

-6.1

-3.4

-15

-6.3

-13

-14

-6

-6

-2.9

0

-1.1

-1

-4

-6.9

0

0

.45

-.2

0

-2.2

-.29

-3.4

-1.8

-.81

-.27

0

.83

-

-

-

-

-

-

-

-

-

-

-2

-

-

-

-

0

-1.2

-.74

-1 

0

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Site 

number

(fig. 5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

31

32

32

33

34

35

38

39

40

43

45

49

50

54

56

57

60

62

64

65

67

69

72

74

74

76

89

89

90

90

91

91

92

D 

0 

D

0 

D

0 

D 

0 

D

0 

D 

0 

D 

0

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

9

10

10

10

10

10

10

10

11

11

10

10

10

10

10

6

10

10

10

75

64

64

61

65

79

79

67

70

49

81

72

48

74

72

73

61

63

59

61

67

74

36

44

44

65

63

63

66

66

38

38

63

63

75

Dissolved boron (micrograms per liter) Continued

0.22

-.04

-.03

-.01 

.019

.096

-.15 

.071

-.03

-.07

-.02

-.15

-.37

-.06

-.31

-.29

-.14

-.16 

.016

-.16

-.09

-.07

-.11

-.06

-.04

-.29 

.006 

.12 

.05

.24

-.3

-.28

-.06

-.01 

.005

0.026

.76

.85

1

.91

.34 

.13 

.55 

.79 

.63

.90

.17

.012

.57

.0031

.0057

.26

.18

.95

.20

.43 

.51 

.58 

.77 

.84

1

.010

I

.31 

.68 

.027

.093 

.12 

.61 

.96

0.11

.82

.89

1

.92

.48 

.14

.57 

.72 

.74

.92

.25

.054

.56

.029

.27 

.14 

.95 

.080

.27 

.57 

.68 

.81 

.88

1

.040 

L

.54 

.78 

.16

.76 

.97

1

1.1

-.33

-.25

-.36

1

6.3

-11

67

-5

-1.6

-.46

-10

-40

-1.5

-7

-6.9

-3.3

-20

1

-18

-11

-5.9

0

-2.2

-.75

-5.1

0

.12

0

1.5

-7

-.88

-.25

0

0

-

-

-

-

-1

-

-

-

-

-

-

-

-

-

-1

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Site

number 

(fig. 5)

Slope

Censored

data 

treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

92

99

99

99

99

14

14

28

28

35

35

38

38

39

39

40

40

45

45

49

49

54

54

56

56

57

57

76

76

92

D 

0 

D

0 

D

0 

D 

0 

D

0

D 

0 

D 

0 

D

0 

D 

0 

D

0

D 

0 

D 

0 

D

0 

D 

0 

D 

0

10

10

10

13

13

13

13

13

13

13

13

13

13

12

12

13

13

13

13

11

11

13

13

13

13

9

9

11

11

13

75

85

85

124

124

128

128

97

97

114

114

113

113

86

86

99

99

115

115

74

74

92

92

117

117

77

77

89

89

114

Dissolved boron (micrograms per liter) Continued

0.081

.14

.23

0.44

.15

.014

0.60

.24 

.075

Total recoverable cadmium (micrograms per liter)

.32 

.13 .053

.017 

.48

Total recoverable chromium (micrograms per liter)

.21 

.48 

.25 

.38

.32

.51 

.32 

.42

-.01

-.02

.17 

.28 

.19 

.43 

.26

.30

.078

.17

.006

.12

-.14

-.15 

.17 

.21 

.21

0

.000065 

)

.0004 

.00000048 

.00000048

0

0

.0000026

.00000024

.93

.83

.024 

.0002 

.0007 

) 

.0053

.0012

.33

.030

.96

.11

.15

.13

.056

.013

.0002

.011

.0034

.013

.0032

.0093

.0020

.0014

.00093

.95

.86

.085

.016

.017

.0092

.017

.012

.19

.013

.97

.26

.17

.092

.0056

0.75

2

2

.56

0

.42

0

.67

.31

.71

0

0

0 

.31

.5 

0

0

0

0

0

.14

-.17

0

.27 

.25

0

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site 

number

(fig. 5)

Censored 

data 

treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

Total recoverable chromium (micrograms per liter) Continued

92

99

99

D

0

D

13

13

13

114

125

125

0.50

.23

.48

0

.0000091

0

0.0026

.0060

.00059

0.56

0

.56

Total recoverable copper (micrograms per liter)

28

28

32

32

33

33

34

34

35

35

38

38

39

40

40

43

43

45

45

49

49

50

50

54

54

56

56

57

57

62

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

D

0

13

13

13

13

10

10

13

13

13

13

13

13

12

13

13

13

13

13

13

11

11

12

12

13

13

13

13

9

9

12

117

117

103

103

86

86

101

101

114

114

115

115

105

101

101

100

100

115

115

75

75

104

104

110

110

117

117

77

77

97

-.13

.063

-.13

.034

-.1

.033

-.09

-.01

-.19

-.23

-.07

-.07

.095

-.29

-.28

-.13

-.1

-.05

.018

-.01

.009

-.24

-.2

-.15

.006

-.29

-.15

-.23

-.22

-.05

.035

.35

.084

.66

.23

.72

.24

.97

.013

.0021

.34

.34

.24

.0003

.0005

.098

.21

.47

.83

.92

.96

.0014

.0069

.018

.95

.000014

.031

.014

.017

.53

.067

.42

.27

.72

.30

.73

.46

.98

.062

.024

.46

.46

.38

.015

.016

.37

.45

.62

.88

.92

.96

.034

.064

.12

.96

.0059

.10

.68

0

0

0

0

0

0

0

0

-.67

-.68

0

0

.27

-.67

-.5

0

0

0

0

0

0

-.29

0

0

0

-.33

0

-.5

-.29

0

-

-

-

-

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Slope

Site 

number 

(fig. 5)

Censored 

data 

treatment

Years of 

record

Number of 

observations Tau

Adusted 

p-value p-value1 Per year

Per

m

pe

Total recoverable copper (micrograms per liter) Continued

62

64

65

65

67

67

69

76

76

86

86

92

92

99

99

D

0

D

0

D

0

D

0

D

0

D

0

D

12

10

13

13

13

13

13

11

11

13

13

13

13

13

13

97

85

109

109

115

115

121

89

89

120

120

115

115

125

125

-0.07

.18

-.01

-.01

-.02

-.02

-.11

-.28

-.28

-.05

.15

0

.23

-.08

.098

0.38 0.52

.045

.91

.95

.83

.79

.095

.0014

.0017

.42

.023

1 1

.0007

.17

.13

.12

.93

.96

.88

.83

.15

.061

.065

.49

.16

.032

.16

.25

0

.5

0

0

0

0

0

-1.1

-.67

0

0

0

0

0

0

-1

-

Dissolved copper (micrograms per liter)

35

35

38

38

39

39

64

64

0

D

0

D

0

D

0

D

10

10

10

10

10

10

10

10

80

80

78

78

66

66

60

60

-.09

-.12

-.06

-.11

.16

.13

-.2

-.23

.32

.16

.56

.22

.14

.23

.073

.030

.37

.25

.69

.40

.22

.30

.12

.078

0

0

0

0

.78

.15

0

0

Total recoverable iron (micrograms per liter)

14

20

22

28

31

_ 32

3 33

1 34

> 35

01 38

_

--

_

_

-

13

13

13

13

10

13

10

13

13

13

101

84

86

100

89

96

86

94

91

94

.11

-.04

-.07

-.06

0

-.12

-.34

-.25

-.02

.044

.18

.72

.50

.51

1 1

.15

.0002

.0035

.83

.63

.13

.74

.32

.29

.29

.011

.037

.86

.75

23

-3.8

-19

-5.5

-.67

-19

-45

-43

-1.8

15

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-9

Site

number 

(fig- 5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

0) O1 5" 

&

39

40

43

43

45

49

50

54

56

57

60

62

64

65

67

69

72

74

74

76

84

86

90

91

92

93

96

99

43

43

49

49

50

0 

D

12

13

13

13

13

10

12

13

13

9

12

12

10

13

13

13

12

13

13

11

13

13

10

13

10

13

13

13

10

13

10

10

10

10

10

85

94

94

94

92

73

87

85

88

77

83

79

85

84

89

98

100

110

110

89

92

96

80

99

84

86

90

94

83

125

50

50

72

72

49

Total recoverable iron (micrograms per liter) Continued

0

-.03

.023

.023

-.04

.23

.11

-.21

-.35

-.14

.094

-.06

.15

-.04

.11

-.06

.057

_ j

_ j

-!09

-.19

-.02

_ i

.022

_ i

-.17

-.16

-.15

.008

-.07

I

.73

.81

.81

.68

.029

.23

.026

.000091

.16

.33

.57

.11

.69

.22

.53

.51

.20

.20

.34

.031

.87

.30

.82

.27

.061

.071

.093

.97

.33

1

.69

.87

.87

.76

.061

.14

.089

.019

--

.42

.44

.077

.69

.22

.34

.58

.34

.34

.30

.051

.90

.55

.88

.20

.21

.19

.13

.94

.43

Dissolved iron (micrograms per liter)

.01

.031

.036

.025

-.02

1

.87

.77

.84

.93

1

.89

.75

.83

.90

-1

-3.3

12

11

-4.7

89

20

-52

-39

-29

13

-17

25

-7.1

19

-6

7.8

-18

-16

-14

-29

-4

-12

1

-7.5

-10

-21

-28

1

-8.5

-

-

-

-

-

-

-

-

-

-

-

-

-

-

-

-

.33
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Site

number 

(fig. 5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

50

54

54

56

56

40

40

0 

0 

D 

0 

D

0 

D

10

10

10

10

10

13

13

49

78

78

75

75

122

122

Dissolved iron (micrograms per liter) Continued

-0.11

-.28

-.23

-.31

-.01

0.42

.003

.016

.0008

.92

0.12

.079

.13

.018

.94

Total recoverable lead (micrograms per liter)

.045 

.11

.41 

.087

.75 

.53

0

-9.8

-2.6

-2.0 

0

-1

-

-1

Total recoverable manganese (micrograms per liter)

14

20

22

28

31

32

33

34

35

38

39

40

43

45

49

50

54

56

57

60

62

64

65

67

69

13

13

13

13

10

13

10

13

13

13

12

13

13

13

10

12

13

13

9

12

12

10

13

13

13

101

84

86

94

89

82

95

91

97

86

94

93

94

73

87

87

88

77

83

79

81

85

89

97

.005 

.04

-.05

-.12 

.017

-.08

-.27

-.27

-.17

-.07

.20

-.07 

.063

-.15

-.21

.01

-.39

-.3

-.14

-.13

-.13

-.04

-.17

-.27

-.18

.97 

.69 

.60 

.16

.40

.0041

.0014

.061

.43

.033

.44

.48

.087

.046

.94

.000019

.0009

.16

.16

.19

.67

.065

.0023

.030

.98 

.77 

.65 

.10 

.82

.45

.023

.0070

.081

.54

.047

.39

.49

.22

.14

.94

.0022

.024

.25

.27

.74

.12

.011

.095

0

.37

-.56

-.67

.25

-1.5

-6.7

-3.2

-3

-.5

3.4

-1.1

1

-1.2

-4.1

.14

-4

-2

-1.3

-1.3

-2

-.34

-1.8

-2

-2.3

-

-

-

-

-

-

-

-

-

-

-

-

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site 

number 

(fig. 5)

Censored 

data 

treatment

Years of 

record

Number of 

observations Tau p- value

Adusted 

p- value1 Per year

Per

m

pe

Total recoverable manganese (micrograms per liter)

72

74

74

76

84

86

88

89

90

91

92

93

96

99

_

0

D

--

_

..

_

12

13

13

10

13

13

12

13

10

13

13

13

10

13

100

113

113

87

93

97

81

100

80

87

89

96

83

97

-0.13

-.05

-.05

-.18

-.15

.058

-.1

-.04

.056

-.3

-.14

-.01

.031

-.18

0.10

.54

.54

.044

.078

.51

.31

.60

.59

.001

.13

.97

.77

.036

0.27

.64

.64

.015

.054

.61

.49

.50

.69

.021

.16

.96

.75

.096

-1

-.5

-.5

-1.4

-1.8

.4

-1.6

-.35

.5

-2

-1

0

.17

-2.2

-

-

-

-

-

-

-

-

-

Dissolved manganese (micrograms per liter)

14

20

22

28

28

31

32

32

33

34

35

38

39

40

43

_

0

D

_

0

D

~

-

10

7

10

7

7

10

10

10

10

10

10

10

10

10

10

87

59

60

69

69

77

65

65

61

65

82

80

67

70

50

.018

-.01

.015

.16

.10

-.03

.10

.10

-.22

-.18

-.14

-.02

.16

-.12

.19

.87

1

.95

.13

.32

.81

.38

.38

.069

.12

.14

.86

.14

.29

.17

.87

.90

~

.87

.42

.42

.045

.20

.18

.84

.14

.24

.12

.083

-.33

0

.12

0

0

3.5

3.3

-4

-2.5

-1.9

0

2.5

-.9

3.8

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Site

number 

(fig-5)

Censored

data 

treatment

Slope

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

45

49

50

54

56

57

60

62

64

65

67

69

12

12

74

74

76

76

84

84

86

88

88

90

91

91

92

92

93

96

99

99

0 

D 

0

D 

0 

D 

0 

D

0 

D

D 

0 

D

0 

D

Dissolved manganese (micrograms per liter) Continued

10

10

10

10

10

9

10

10

10

10

10

10

10

10

11

11

10

10

10

10

10

10

10

6

10

10

10

10

10

10

10

10

81

12

49

78

75

75

63

64

61

63

67

76

41

41

46

46

68

68

80

80

70

65

65

39

66

66

76

76

60

68

86

-0.05

-.25

-.11

-.26

-.24

-.19 

.14

-.29

-.36

-.45

-.42

-.21

-.07

-.11

-.09

-.12

-.34

-.35

-.24

-.24

.092

-.34

-.32

-.1

-.15

-.23

-.02

-.07 

.12 

.15

-.09

-.08

0.61

.016

.45

.0091

.016

.058

.23

.011

.0021

.000081

.0001

.035

.73 

.56 

.55

.43 !ooi6

.0009

.012

.012

.41

.0013

.0016

.62

.18

.04 

.88 

.46 

.34 

.18

.26 

.29

0.54

.064

.61

.018

.11

.18

.11

.088

.030

.50 

.18 

.81 

.70 

.65

.55

.010

.0099

.078

.078

.22

.041

.048

.37

.18 

.88 

.44 

.39

.27

.39 

.40

-0.54

-4.5

-1.5

-3

-1.4

-1.3

1

-4.8

-3.5

-4.5

-2.8

-1

0

0

0

0

-1.4

-.88

-.79

-.75

.6

-1.1

-.33

-1.4

-.75

-.6

0

0

1.2

.89

0

0

-

-

-

-

-

-

-

-

-1

-

-

-

-

-

-

-1

-

-

-

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site

number 

(fig. 5)

Censored

data 

treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Perc

me

per 

28

28

35

35

38

38

39

39

40

40

49

49

50

50

54

54

56

56

57

57

62

62

64

64

76

76

86

86

35

35

38

38

39

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D 

0 

D 

0

D 

0 

D 

0 

D

0 

D 

0 

D 

0

D 

0 

D

10

10

10

10

11

11

10

10

10

10

10

10

11

11

11

11

10

10

9

9

10

10

10

10

10

10

10

10

10

10

10

10

10

89

89

89

89

89

89

84

84

86

86

73

73

86

86

84

84

80

80

77

77

78

78

81

81

87

87

88

88

82

82

80

80

66

Total recoverable nickel (micrograms per liter)

-0.11

-.06

.20

.26

0

.072

.35

.43

.13

.16

.12

.17

.088

.11

.037

.16

-.46

-.46

-.39

-.36

.026

.14

.18

.24

-.13

-.12

-.22

-.12

0.17 0.20

.46

.021

.0028

1 1

.43

.000035

.00000072

.15

.080

.23

.071

.28

.19

.68

.068

.0000010

.0000012

.000078

.0003

.81

.15

.043

.0068

.16

.17

.011

.17

.53

.10

.040

.34

.012

.0055

.30

.27

.23

.11

.22

.20

.72

.20

.0056

.0055

~

.82

.24

.11

.056

.18

.19

.072

.30

Dissolved nickel (micrograms per liter)

.093

.11

-.07

-.05

.18

.31

.23

.44

.65

.090

.33

.18

.46

.66

.078

.4 

.5 

0

0

1.2

1

0

.063

2

1

0

0

0

0

0

0

-2

-2

-1.8

-1.7

0

.15

0

.23

-.5

-.33

-.54

-.083

-

-

-1

-

-4

-

-7

-
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site 

number

(fig. 5)

Censored

data 

treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Perc

me

pe

39

40

40

56

56

57

57

62

62

76

76

86

86

D 

0 

D 

0 

D

0 

D 

0 

D 

0

D 

0 

D

10

10

10

10

10

9

9

10

10

10

10

10

10

66

71

71

71

71

72

72

62

62

67

67

69

69

Dissolved nickel (micrograms per liter) Continued

0.18

.075

.08

-.38

-.37

-.38

-.35

-.06 

.036

-.25

-.2

-.16

-.02

0.080

.45

.40

.0002

.0004

.0002

.0006

.64

.79

.019

.067

.13

.87

0.096

.56

.53

.027

.025

.51 

.76 

.092

.073

.19

.89

0

0

0

-1.8

-1.8

-1.8

-1.5 

0 

0

-.63

-.5

0

0

-

-

-1

-1

-

-

28

28

14

20

22

28

31

32

33

34

35

38

40

43

45

49

50

0 

D

10

11

11

10

10

10

10

10

10

10

10

10

10

10

10

38

38

93

82

82

89

82

82

87

90

86

87

86

88

74

85

Total recoverable selenium (micrograms per liter)

1 -.02

-.05 .81

Total recoverable strontium (micrograms per liter)

.24 

.24 

.20 

.19 

.18

.16 

.18 

.082 

.05

.12

.14

.20

.13

.005

.63

.0058

.013

.035

.039

.048

.096

.057

.38

.56

.22

.12

.033

.17

.083

.034

.082

.056

.17

.082 

.14 

.45 

.66

.33

.067 

.14 

.17 

I 

.0017

1

1.4 

6

3.2

4

1.7

19

12

8.6

-9.3

-26

-19 

6

-7.0 

1.2

-93

-

-

-

-

-2
Table A5. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site Censored 

number data 

(fig. 5) treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

Total recoverable strontium (micrograms per liter) Continued

54

56

57

60

62

64

65

67

69

72

74

76

84

86

88

89

90

91

92

93

96

99

10

10

9

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

10

84

81

77

82

78

81

76

81

89

81

82

88

86

87

81

93

80

81

81

84

84

94

-0.23

-.44

-.35

.13

-.58

-.13

.055

.079

.089

.055

.02

-.16

.28

.23

.32

.21

.14

.26

.33

.10

.054

.29

0.013

.0000032

.0004

.18

.0000000045

.17

.62

.43

.33

.59

.87

.08

.0025

.011

.0008

.018

.16

.0061

.0005

.28

.59

.0007

0.15

.0065

.20

.0089

.18

.46

.29

.29

.56

.86

.15

.012

.19

.093

.23

.27

.11

.067

.45

.64

.085

-5.4

-6.6

-8.8

7.1

-92

-15

7.8

6.2

10

.5

.39

-3.1

39

2

25

12

2

16

21

1.3

.5

14

-

-

-

-1

-

-

Dissolved strontium (micrograms per liter)

14

20

22

28

31

32

33

34

35

38

10

7

10

7

10

10

10

10

10

10

83

58

59

67

73

63

58

65

81

80

.16

.16

.19

.19

.051

.25

.15

.14

-.02

-.2

.089

.22

.12

.092

.65

.030

.26

.23

.87

.042

.27

.20

.70

.030

.32

.36

.91

.12

1

6.3

5.7

5.2

.8

26

12

1.4

-6.8

-44

-

-
Table AS. Trend-test results and median concentrations for elements in stream water in the upper Illinois River Basin, 1978-90 

Slope

Site Censored 

number data 

(fig. 5) treatment

Years of 

record

Number of 

observations Tau p-value

Adusted 

p-value1 Per year

Per

m

pe

Dissolved strontium (micrograms per liter) Continued

40

43

45

49

50

54

56

57

60

62

64

65

67

69

72

74

76

84

86

88

89

90

91

92

93

96

99

10

10

10

10

10

10

10

9

10

10

10

10

10

10

10

10

10

10

10

10

10

6

10

10

10

10

10

69

50

81

72

47

76

72

73

62

61

60

61

67

73

40

41

66

77

62

66

67

35

65

76

59

68

83

-0.16

.19

-.08

-.03

-.62

-.34

-.44

-.36

.11

-.67

-.16

0

-.04

-.02

0

-.16

-.2

.32

.079

.32

.37

-.03

.31

.41

.13

.099

.28

0.15

.18

.42

.84

.000022

.0007

.000024

.0005

.35

.000000014

.21

1

.78

.88

1

.38

.069

.0013

.53

.0043

.001

1

.0066

.000044

.33

.39

.0027

0.14

.31

.36

.79

.0015

.058

.0043

.23

.0072

.15

1

.67

.86

1

.51

.17

.0093

.75

.13

.074

.13

.034

.51

.43

.075

-22

9.1

-5.8

-2.8

-75

-8

-6.9

-9.5

6.5

-120

-21

.7

-3.4

-3.2

0

-6.3

-4

45

1.5

23

19

-.5

21

23

1.7

.81

13

-

-

-2

-

-

-

-2

-

-

-

P-value adjusted for serial correlation when there were 10 or more years of record.
APPENDIX B. MINIMUM REPORTING LEVELS AND ANALYTICAL METHODS FOR 

MAJOR AND TRACE ELEMENTS IN WATER, SEDIMENT, AND BIOTA

Table B1 contains data on the minimum reporting levels and analytical methods for elements in water, sediment, and 

biota.

250 Major and Trace Elements in Water, Sediment, and Biota, 1978-90
Table B1. Minimum reporting levels and chemical analytical methods for major and trace elements in the upper 

Illinois River Basin

[ftg/L, micrograms per liter; , missing method; ug/g, micrograms per gram; mg/g, milligrams per gram; fig, microgram]

Laboratory abbreviations: IEPA, Illinois Environmental Protection Agency Laboratory, Chicago or Champaign, 111.; USGS2, U.S. Geological Survey, 

Geologic Division, Branch of Geochemistry, Menlo Park, Calif.; USGS, U.S. Geological Survey, National Water Quality Laboratory, Denver, Colo.; 

ETSRC, Environmental Trace Research Center.

Analytical method: AA, direct atomic absorption; ICP-AES, inductively coupled plasma-atomic emission spectroscopy; CV-AAS, atomic absorption 

spectroscopy after mercury vapor generation; AAS, atomic absorption spectroscopy; Hydride-AAS, atomic absorption spectroscopy after elementhydride generation; ICP-MS, inductively coupled plasma-mass spectrometry; GF-AAS, graphite furnace, atomic absorption spectroscopy.

Decomposition method: HC1, HNO3, HC1O4, HF, total digestion by use of the indicated acids; HNO3, Na2Cr2O7, total digestion by use of the indicated 

compounds; hot water dissolution was the partial digestion technique used for boron; combustion was the decomposition technique used for sulfur and 

total carbon; partial HNO3, partial digestion by use of the acid indicated.

Element

Aluminum, dissolved (\Lg/L as Al)

Aluminum, total recoverable

(H.g/L as Al)

Aluminum, sediment, suspended

(percent as Al)

Aluminum, sediment, streambed

(percent as Al)

Aluminum, fish (H-g/g dry weight)

Aluminum, invertebrate (|ig/g dry weight)

Aluminum, plant (|ig/g dry weight)

Aluminum, crustaceans (Jig/g dry weight)

Antimony, dissolved (^ig/L as Sb)

Antimony, sediment, suspended

(lig/g as Sb)

Antimony, sediment, streambed (H-g/g)

Arsenic, dissolved (^ig/L as As)

Arsenic, total recoverable (|j,g/L as As)

Arsenic, sediment, suspended

(H.g/g as As)

Arsenic, sediment, streambed (fig/g)

Arsenic, fish (Jig/g dry weight)

Arsenic, invertebrate (|ig/g dry weight)

Arsenic, plant (p.g/g dry weight)

Arsenic, crustaceans (H-g/g dry weight)

Barium, dissolved (|ig/L as Ba)

Barium, total recoverable (|ig/L as Ba)

Barium, sediment, streambed (^ig/g)

Barium, fish (H-g/g dry weight)

Barium, invertebrate (H-g/g dry weight)

Barium, plant (|J,g/g dry weight)

Barium, crustaceans (^ig/g dry weight)

Beryllium, dissolved (H£/L as Be)

Beryllium, total recoverable

(H-g/L as Be)

Beryllium, sediment, suspended

(lig/g as Be)

Beryllium, sediment, streambed Qig/g)

Beryllium, fish (fig/g dry weight)

Beryllium, invertebrate (|ig/g dry weight)

Beryllium, plant (H-g/g dry weight)

Beryllium, crustaceans (|J,g/g dry weight)

Boron, dissolved (^ig/L as B)

Minimum 

reporting level

50

50

.01

1.0

3

3

3

3

1

.1

.1

1

1

1-5

.1

.2

.2-1

.1-.2

.2

5

5

1

.1

.1

.1

.1

.5-2

.5-2

1-2

1

.1

.1

.1

.1

50

Laboratory

ffiPA

USGS2

ffiPA

USGS

ETSRC

ETSRC

ETSRC

ETSRC

USGS

USGS2

USGS

ffiPA

USGS

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

Analytical 

method

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

AA

ICP-MS

Hydride-AAS

ICP-AES

ICP-AES

ICP-MS

Hydride-AAS

Hydride-AAS

Hydride-AAS

Hydride-AAS

Hydride-AAS

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

Decomposition 

method

-

HCl/HNCy HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

._

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HC1/HN03/HC104/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

-

Table B1 251
Table B1. Minimum reporting levels and chemical analytical methods for major and trace elements in the upper 

Illinois River Basin Continued

Element

Boron, total recoverable (|ig/L as B)

Boron, sediment, streambed (|ig/g)

Boron, fish (ng/g dry weight)

Boron, invertebrate (|ig/g dry weight)

Boron, plant (^ig/g dry weight)

Boron, crustaceans (|ig/g dry weight)

Cadmium, dissolved (|ig/L as Cd)

Cadmium, total recoverable (yg/L as Cd)

Cadmium, sediment, suspended

(yg/g as Cd)

Cadmium, sediment, streambed (jig/g)

Cadmium, fish (^ig/g dry weight)

Cadmium, invertebrate (|ig/g dry weight)

Cadmium, plant (|ig/g dry weight)

Cadmium, crustaceans (^ig/g dry weight)

Chromium, dissolved (|ig/L as Cr)

Chromium, total recoverable (jig/L as Cr)

Chromium, sediment, suspended

(yg/g as Cr)

Chromium, sediment, streambed (jig/g)

Chromium, fish (jig/g dry weight)

Chromium, invertebrate (^ig/g dry weight)

Chromium, plant (H-g/g dry weight)

Chromium, crustaceans (^ig/g dry weight)

Cobalt, dissolved (\LgfL as Co)

Cobalt, total recoverable (|ig/L as Co)

Cobalt, sediment, suspended (^ig/g as Co)

Cobalt, sediment, streambed (jig/g)

Copper, dissolved (^ig/L as Cu)

Copper, total recoverable (^ig/L as Cu)

Copper, sediment, suspended

(yg/g as Cu)

Copper, sediment, streambed (jig/g)

Copper, fish (|ig/g dry weight)

Copper, invertebrate (ng/g dry weight)

Copper, plant (^ig/g dry weight)

Copper, crustaceans (^ig/g dry weight)

Iron, dissolved (^ig/L as Fe)

Iron, total recoverable (^ig/L as Fe)

Iron, sediment, suspended

(percent as Fe)

Iron, sediment, streambed

(percent as Fe)

Iron, fish (^ig/g dry weight)

Iron, invertebrate (jig/g dry weight)

Iron, plant (^ig/g dry weight)

Iron, crustaceans (^ig/g dry weight)

Lead, dissolved (\igfL as Pb)

Lead, total recoverable (^ig/L as Pb)

Lead, sediment, suspended Oig/g as Pb)

Lead, sediment, streambed (jig/g)

Lead, fish (|ig/g dry weight)

Lead, invertebrate (^ig/g dry weight)

Lead, plant (^ig/g dry weight)

Lead, crustaceans (^ig/g dry weight)

Minimum 

reporting level

50

.4

2-3

2

2

2

.1-3

.1-3

.1-3

.1

.2-.5

.2

.2

.2-.3

5-10

5

2

1

1-2

1

1

1

5-10

5-10

2

1

5-10

5-10

2

1

.2

.2-.3

.2

.2

5-10

50

.01

.05

1

1

1

1

5-100

5-100

.1

4

4-6

4-6

4

4

Laboratory

ffiPA

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

Analytical 

method

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

GF-AAS

GF-AAS

ICP-MS

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

GF-AAS

GF-AAS

ICP-MS

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

Decomposition 

method

Hot-water dissolution

HNO3/HC1O4

HNO3/HC1O4

HN03/HC104

HNO3/HC1O4

-

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

__

-

HC1/HNO3/HC1O4/HF

HNOVHCICL

HN03/HC104

HNO3/HC1O4

HNO3/HC1O4

--

HC1/HNO3/HC1O4/HF

-

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

._

HC1/HN03/HC104/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

Table B1 252
Table B1 . Minimum reporting levels and chemical analytical methods for major and trace elements in the upper 

Illinois River Basin Continued

Element

Manganese, dissolved (|J.g/L as Mn)

Manganese, total recoverable

((Xg/L as Mn)

Manganese, sediment, suspended

((ig/g as Mn)

Manganese, sediment, streambed (|ig/g)

Manganese, fish Qig/g dry weight)

Manganese, invertebrate

(|Xg/g dry weight)

Manganese, plant (p.g/g dry weight)

Manganese, crustaceans

(p.g/g dry weight)

Mercury, dissolved (p.g/L as Hg)

Mercury, total recoverable (|J.g/L as Hg)

Mercury, sediment, streambed (|J.g/g)

Mercury, fish (|J.g/g dry weight)

Mercury, invertebrate (|lg/g dry weight)

Mercury, plant (|J.g/g dry weight)

Mercury, crustaceans (|J.g/g dry weight)

Molybdenum, dissolved (jig/L as Mo)

Molybdenum, sediment, suspended

(p.g/g as Mo)

Molybdenum, sediment, streambed

Molybdenum, fish (p-g/g dry weight)

Molybdenum, invertebrate

(p,g/g dry weight)

Molybdenum, plant (p.g/g dry weight)

Molybdenum, crustaceans

(^ig/g dry weight)

Nickel, dissolved (p,g/L as Ni)

Nickel, total recoverable (p.g/L as Ni)

Nickel, sediment, suspended

(H.g/g as Ni)

Nickel, sediment, streambed (jig/g)

Nickel, fish (|J.g/g dry weight)

Nickel, invertebrate (p.g/g dry weight)

Nickel, plant (p.g/g dry weight)

Nickel, crustaceans (p-g/g dry weight)

Selenium, dissolved (jig/L as Se)

Selenium, total recoverable (|J.g/L as Se)

Selenium, sediment, streambed (jxg/g)

Selenium, fish (|J.g/g dry weight)

Selenium, invertebrate (|J.g/g dry weight)

Selenium, plant (jig/g dry weight)

Selenium, crustaceans (|J.g/g dry weight)

Silver, dissolved (p.g/L as Ag)

Silver, total recoverable (^.g/L as Ag)

Silver, sediment, suspended

(jig/g as Ag)

Silver, sediment, streambed

(\ig/g as Ag)

Silver, fish (p.g/g dry weight)

Silver, invertebrate (p.g/g dry weight)

Silver, plant (M-g/g dry weight)

Silver, crustaceans (|J.g/g dry weight)

Minimum 

reporting level

5

5

2

4

.2-.3

.2-.3

.2

.2

.05-.!

.05-.!

.02

.005

.005-.008

.005-.007

.005

10

.001

2

1

1

1

1

5-50

5-50

4

2

1-2

2

2

2

1

1

.1

.1-.3

.1

.1-.2

.1

3-5

3-5

.1-2

2

2-3

2

2

2

Laboratory

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS

ETSRC

ETSRC

ETSRC

ETSRC

USGS

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

USGS

ETSRC

ETSRC

ETSRC

ETSRC

Analytical 

method

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

AAS

AA

CV-AAS

CV-AAS

CV-AAS

CV-AAS

CV-AAS

ICP-AES

ICP-MS

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

Hydride-AAS

Hydride-AAS

Hydride-AAS

Hydride-AAS

Hydride-AAS

ICP-AES

ICP-AES

ICP-MS

_.

ICP-AES

ICP-AES

ICP-AES

ICP-AES

Decomposition 

method

-

~

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HN03/Na2Cr207

HNO3

HNO3

HNO3

HNO3

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

~

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HN03/HC104/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNOyHC104

__

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

Table B1 253
Table B1 . Minimum reporting levels and chemical analytical methods for major and trace elements in the upper 

Illinois River Basin Continued

Element

Strontium, dissolved (|ig/L as Sr)

Strontium, total recoverable (|ig/L as Sr)

Strontium, sediment, streambed

(^ig/g as Sr)

Strontium, fish (|ig/g dry weight)

Strontium, invertebrate (|Xg/g dry weight)

Strontium, plant (|ig/g dry weight)

Strontium, crustaceans (|ig/g dry weight)

Vanadium, dissolved (|ig/L as V)

Vanadium, total recoverable (p.g/L as V)

Vanadium, sediment, suspended

Qig/g as V)

Vanadium, sediment, streambed

(|ig/g as V)

Vanadium, fish (|ig/g dry weight)

Vanadium, invertebrate (|ig/g dry weight)

Vanadium, plant (|ig/g dry weight)

Vanadium, crustaceans (|ig/g dry weight)

Zinc, dissolved (|ig/L as Zn)

Zinc, total recoverable Qig/L as Zn)

Zinc, sediment, suspended (|ig/g as Zn)

Zinc, sediment, streambed (|ig/g as Zn)

Zinc, fish (jig/g dry weight)

Zinc, invertebrate (|ig/g dry weight)

Zinc, plant (|ig/g dry weight)

Zinc, crustaceans (jxg/g dry weight)

Minimum 

reporting level

5

5

2

.1

.1-3

.1

.2

5-10

5-10

4

2

.3-.4

.3-.4

3

.3

50-100

50-100

4

4

.2-.5

.2-3

.2-3

3

Laboratory

ffiPA

ffiPA

uses

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

uses

ETSRC

ETSRC

ETSRC

ETSRC

ffiPA

ffiPA

USGS2

uses

ETSRC

ETSRC

ETSRC

ETSRC

Analytical 

method

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

ICP-AES

Decomposition 

method

..

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNC>3/HC1O4

~

HC1/HNO3/HC1O4/HF

HN03/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HC1/HNO3/HC1O4/HF

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

HNO3/HC1O4

Table B1 254