Cover photo: Black River Harbor, Lorain, Ohio. Photo by Paul Baumann,

U.S. Geological Survey, Columbus, Ohio.
U.S. Department of the Interior

U.S. Geological Survey

Areal Distribution and Concentrations of 

Contaminants of Concern in Surficial 

Streambed and Lakebed Sediments, 

Lake Erie-Lake Saint Clair Drainages, 

1990–97 

By S.J. Rheaume, D.T. Button, D.N. Myers, and D.L. Hubbell

Water-Resources Investigations Report 00-4200
U.S. Department of the Interior

GALE A. NORTON, Secretary

U.S. Geological Survey

Charles G. Groat, Director 

Any use of trade, product, or firm names is for

descriptive purposes only and does not imply

endorsement by the U.S. Government.

_____________________________________________________________________________________________

For additional information write to:

District Chief

U.S. Geological Survey

6520 Mercantile Way, Ste. 5

Lansing, Michigan 48911-5991

Copies of this report can be purchased from:

U.S.Geological Survey

Branch of Information Services

Box 25286

Denver, CO 80225-0286

Lansing, Michigan

2001
FOREWORD 

The U.S. Geological Survey (USGS) is committed to serve the Nation with accurate and timely scientific 

information that helps enhance and protect the overall quality of life, and facilitates effective management of 

water, biological, energy, and mineral resources. (http://www.usgs.gov/). Information on the quality of the 

Nation’s water resources is of critical interest to the USGS because it is so integrally linked to the long-term 

availability of water that is clean and safe for drinking and recreation and that is suitable for industry, irrigation, 

and habitat for fish and wildlife. Escalating population growth and increasing demands for the multiple water 

uses make water availability, now measured in terms of quantity and quality, even more critical to the long-term 

sustainability of our communities and ecosystems. 

The USGS implemented the National Water-Quality Assessment (NAWQA) Program to support national, 

regional, and local information needs and decisions related to water-quality management and policy. 

(http://water.usgs.gov/nawqa). Shaped by and coordinated with ongoing efforts of other Federal, State, and local 

agencies, the NAWQA Program is designed to answer: What is the condition of our Nation’s streams and ground 

water? How are the conditions changing over time? How do natural features and human activities affect the 

quality of streams and ground water, and where are those effects most pronounced? By combining information 

on water chemistry, physical characteristics, stream habitat, and aquatic life, the NAWQA Program aims to 

provide science-based insights for current and emerging water issues and priorities. NAWQA results can 

contribute to informed decisions that result in practical and effective water-resource management and strategies 

that protect and restore water quality. 

Since 1991, the NAWQA Program has implemented interdisciplinary assessments in more than 50 of the 

Nation’s most important river basins and aquifers, referred to as Study Units. 

(http://water.usgs.gov/nawqa/nawqamap.html). Collectively, these Study Units account for more than 60 percent 

of the overall water use and population served by public water supply, and are representative of the Nation’s 

major hydrologic landscapes, priority ecological resources, and agricultural, urban, and natural sources of 

contamination. 

Each assessment is guided by a nationally consistent study design and methods of sampling and analysis. The 

assessments thereby build local knowledge about water-quality issues and trends in a particular stream or aquifer 

while providing an understanding of how and why water quality varies regionally and nationally. The consistent, 

multi-scale approach helps to determine if certain types of water-quality issues are isolated or pervasive, and 

allows direct comparisons of how human activities and natural processes affect water quality and ecological 

health in the Nation’s diverse geographic and environmental settings. Comprehensive assessments on pesticides, 

nutrients, volatile organic compounds, trace metals, and aquatic ecology are developed at the national scale 

through comparative analysis of the Study-Unit findings. (http://water.usgs.gov/nawqa/natsyn.html). 

The USGS places high value on the communication and dissemination of credible, timely, and relevant science 

so that the most recent and available knowledge about water resources can be applied in management and policy 

decisions. We hope this NAWQA publication will provide you the needed insights and information to meet your 

needs, and thereby foster increased awareness and involvement in the protection and restoration of our Nation’s 

waters. 

The NAWQA Program recognizes that a national assessment by a single program cannot address all waterresource issues of interest. External coordination at all levels is critical for a fully integrated understanding of 

watersheds and for cost-effective management, regulation, and conservation of our Nation’s water resources. The 

Program, therefore, depends extensively on the advice, cooperation, and information from other Federal, State, 

interstate, Tribal, and local agencies, non-government organizations, industry, academia, and other stakeholder 

groups. The assistance and suggestions of all are greatly appreciated. 

 Robert M. Hirsch 

 Associate Director for Water 
ACKNOWLEDGMENTS

Technical Support

John Estenik, Ohio Environmental Protection Agency, Columbus, Ohio

Charles Staudt, Ohio Environmental Protection Agency, Columbus, Ohio

Gary Kohlhepp, Michigan Department of Environmental Quality, Lansing, Michigan

Scott Painter, Environment Canada, Burlington, Ontario

Francine Norling, U.S. Environmental Protection Agency, Region 5, Chicago, Illinois

Dora R. Passino-Reader, U.S. Geological Survey, Ann Arbor, Michigan

Technical and Colleague Reviewers

Stephen B. Smith, U.S. Geological Survey, Reston, Virginia

Thomas J. Lopes, U.S. Geological Survey, Rapid City, South Dakota

Editorial and Graphics

C. Michael Eberle, U.S. Geological Survey, Columbus, Ohio

Sharon B. Baltusis, U.S. Geological Survey, Lansing, Michigan

Amy D. Sutton, U.S. Geological Survey, Lansing, Michigan

Approving Officials

James R. Nicholas, U.S. Geological Survey, Lansing, Michigan

Chester Zenone, U.S. Geological Survey, Reston, Virginia

IV Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie-

 Lake Saint Clair Drainages, 1990–97
Abstract . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 1

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

Purpose and scope . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4

Background. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5

Study design . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5

Study methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7

Sampling agencies and analyzing laboratories . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7

Other screening criteria . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8

Sediment-quality guidelines selected for comparison with site data. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9

Guidelines selected . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9

Statistical and graphical methods. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10

Areal distribution and concentrations of contaminants of concern in surficial bed sediments . . . . . . . . . . . . . . . . . . . . 11

Organochlorine compounds. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11

Total chlordane. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11

Total DDT . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12

Total dieldrin . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12

Hexachlorobenzene. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15

Total hexachlorocyclohexane . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15

Lindane . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15

Total mirex . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15

Total PCB . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 18

Polycyclic aromatic hydrocarbons . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 18

Total PAH . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 18

Anthracene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20

Benz[a]anthracene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20

Benzo[a]pyrene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20

Chrysene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 22

Phenanthrene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 22

Trace metals . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 25

Arsenic . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 25

Cadmium . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 25

Copper . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 27

Lead . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 27

Mercury . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 27

Zinc. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 29

Sediment contamination and potential impairments of aquatic life . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 29

Occurrence and magnitude of potential impairments. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 29

Contamination within and outside of Areas of Concern . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 31

Comparative ranks by location . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 34

Summary . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 37

CONTENTS

Contents V
References cited . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 38

Appendixes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 41

FIGURES

1-3. Maps showing:

1. Location of Lake Erie–Lake Saint Clair Drainages study unit, principal streams, and 

major cities . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2

2. Land use/land cover in the Lake Erie–Lake Saint Clair Drainages, 1992 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6

3. Location of bed-sediment samples analyzed for potential contaminants in the Lake Erie–

Lake Saint Clair Drainages, 1990–97. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6

4-23. Maps showing location of bed-sediment samples and concentration range of contaminants of 

concern in the Lake Erie–Lake Saint Clair Drainages, 1990–97: 

4. Total chlordane . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14

5. Total DDT . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14

6. Total dieldrin . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 16

7. Hexachlorobenzene. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 16

8. Total hexachlorocyclohexane . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 17

9. Lindane. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 17

10. Total mirex . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 19

11. Total PCB . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 19

12. Total PAH . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21

13. Anthracene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 21

14. Benz[a]anthracene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 23

15. Benzo[a]pyrene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 23

16. Chrysene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24

17. Phenanthrene . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 24

18. Arsenic. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 26

19. Cadmium . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 26

20. Copper . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 28

21. Lead . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 28

22. Mercury . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 30

23. Zinc . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 30

24. Histogram showing frequency of detection and percentage of sample concentrations exceeding 

a sediment-quality guideline, Lake Erie–Lake Saint Clair Drainages, 1990–97 . . . . . . . . . . . . . . . . . . . . . . . 32

25. Map showing Areas of Concern (in red) in the Lake Erie–Lake Saint Clair Drainages . . . . . . . . . . . . . . . . . 32

26. Star diagrams showing 75th and 90th percentile concentrations of selected trace element 

contaminants in relation to sediment-quality guidelines within and outside of Areas of Concern, 

Lake Erie–Lake Saint Clair Drainages, 1990–97 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 34

27. Star diagrams showing 75th and 90th percentile concentrations of selected organic compound 

contaminants in relation to sediment-quality guidelines within and outside Areas of Concern, 

Lake Erie–Lake Saint Clair Drainages, 1990–97 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 35

VI Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake

Erie-Lake Saint Clair Drainages, 1990–97
TABLES

1. Organic compounds and trace metals in bed sediment identified by the Lake Erie Lakewide 

Management Plan (LaMP) as chemical contaminants of concern in the Lake Erie Basin,

United States and Canada . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 3

2. Selected guidelines for chemical concentrations in freshwater bed sediment that have been 

observed or predicted to be associated with adverse effects on aquatic biota . . . . . . . . . . . . . . . . . . . . . 10

3. Number of bed-sediment samples reported, number with detected values, and the number detected

in relation to sediment-quality guidelines, Lake Erie–Lake Saint Clair Drainages, 1990–97 . . . . . . . . . . . . 13

4. Probability of sample concentrations being equal to or greater than a sediment-quality guideline, 

Lake Erie–Lake Saint Clair Drainages, 1990–97 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 33

5. Ten river basins with highest levels and frequencies of bed-sediment contamination in the Lake-Erie–

Lake Saint Clair Drainages, 1990–97. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 36

APPENDIX A

Methods of sample collection, analysis, quality assurance, and quality control . . . . . . . . . . . . . . . . . . . . . . . . . 42

Table A1. Chemical class, number of agencies providing data bases, and number of analyzing 

laboratories contributing sediment-quality data, 1990-97. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 43

Table A2. Summary of sample-collection methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 43

Table A3. Summary of sample preparation and analysis methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 44

Table A4. Summary of quality-assurance programs and quality-control procedures . . . . . . . . . . . . . . . . . . . . . 45

APPENDIX B

Figures B1-B2. Graphs showing probability distributions of concentrations and detection limits

for streambed and lakebed sediments in relation to sediment-quality guidelines, Lake Erie–Lake

Saint Clair Drainages, 1990-97 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 46

APPENDIX C

Development of bed-sediment-quality guidelines in Canada and the United States. . . . . . . . . . . . . . . . . . . . . . 58

Sediment effect concentrations--classifying toxicity of United States Great Lakes sediment . . . . . . . . . . . . . 58

Sediment quality assessment values for ecosystems in Canada and the Great Lakes . . . . . . . . . . . . . . . . . . . . 59

Contents VII
CONVERSION FACTORS AND ABBREVIATIONS

Multiply By To obtain

Length mile (mi) 1.609 kilometer

Area square mile (mi2

) 2.590 square kilometer

Weight milligram (mg) 0.00003527 ounce, avoirdupois

kilogram (kg) 2.205 pound, avoirdupois

Abbreviated water-quality units used in this report: Chemical concentrations for bed sediment are given in milligrams per 

kilogram (mg/kg), a unit expressing the concentration of chemical constituents in bed sediment (dry weight) for synthetic organic 

compounds and trace elements. Numerical values expressed as milligrams per kilogram are the same as concentrations in parts per

million (ppm).

MISCELLANEOUS ABBREVIATIONS 

NAWQA National Water-Quality Assessment

LERI Lake Erie-Lake Saint Clair Drainages study unit

IJC International Joint Commission

LaMP Lakewide Management Plan

RAP Remedial Action Plan

PCB Polychlorinated biphenyl

PAH Polycyclic aromatic hydrocarbon

SVOC Semi-volatile organic compound

NSI National Sediment Inventory

OSI Ohio Sediment Inventory

FIELDS Fully Integrated Environmental Locational Decision Support system

AOC Areas Of Concern (Identified by the International Joint Commission)

GLWQA Great Lakes Water Quality Agreement

USEPA U.S. Environmental Protection Agency

OME Ontario Ministry of Environment

Ohio EPA Ohio Environmental Protection Agency

MDNR Michigan Department of Natural Resources

USGS U.S. Geological Survey

TOC Total Organic Carbon

STORET Storage and Retrieval (U.S. Environmental Protection Agency data system)

USACE U.S. Army Corps of Engineers

EMAP Environmental Monitoring and Assessment Program

SED BIO Sediment data Biological (data collected by Ohio Environmental Protection Agency)

BHC Hexachlorocyclohexane

TEL Threshold Effect Level

PEL Probable Effect Level

LEL Lowest Effect Level

SEL Severe Effect Level

VIII Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake ErieLake Saint Clair Drainages, 1990–97
Abstract 1

Areal Distribution and Concentrations of 

Contaminants of Concern in Surficial Streambed 

and Lakebed Sediments, Lake Erie–Lake Saint Clair 

Drainages, 1990–97

By S. J. Rheaume, D. T. Button, D. N. Myers, and D. L. Hubbel

Abstract 

Concerns about elevated concentrations of contaminants such as polychlorinated biphenyls and 

mercury in aquatic bed sediments throughout the 

Great Lakes Basin have resulted in a need for better understanding of the scope and severity of the 

problem. Various organochlorine pesticides, polychlorinated biphenyls, trace metals, and polycyclic aromatic hydrocarbons are a concern because 

of their ability to persist and accumulate in 

aquatic sediments and their association with 

adverse aquatic biological effects. The areal distribution and concentrations in surficial bed sediments of 20 contaminants of concern with 

established bed-sediment-toxicity guidelines were 

examined in relation to their potential effects on 

freshwater aquatic biota. Contaminants at more 

than 800 sampling locations are characterized in 

this report. Surficial bed-sediment-quality data 

collected from 1990 to 1997 in the Lake Erie–

Lake Saint Clair Drainages were evaluated to 

reflect recent conditions. In descending order, 

concentrations of total polycyclic aromatic hydrocarbons, phenanthrene, total polychlorinated 

biphenyls, chrysene, benz[a]anthracene, 

benzo[a]pyrene, cadmium, lead, zinc, arsenic, and 

mercury were the contaminants that most commonly exceeded levels associated with probable 

adverse effects on aquatic benthic organisms. The 

highest concentrations of most of these contaminants in aquatic bed sediments are confined to the 

12 specific geographic Areas of Concern identified in the 1987 Revisions to the Great Lakes 

Water Quality Agreement of 1972. An exception 

is arsenic, which was detected at concentrations 

exceeding threshold effect levels at many locations outside Areas of Concern.

Introduction 

The Lake Erie–Lake Saint Clair Drainages (fig. 1) 

covers approximately 22,300 mi2 in parts of Indiana, 

Michigan, Ohio, Pennsylvania, and New York. This 

area is one of a select set of hydrologic systems 

(referred to as study units) throughout the Nation that 

were studied between 1991 and 2000 as part of the 

U.S. Geological Survey’s National Water-Quality 

Assessment (NAWQA) Program. The program was 

established to (1) provide a nationally consistent 

description of recent water-quality conditions for a 

large part of the Nation’s freshwater streams and aquifers, (2) define long-term trends in water quality, and 

(3) identify, describe, and explain, where possible, the 

major natural and anthropogenic factors that affect 

water-quality conditions and trends (Hirsch and others, 1988).

Anthropogenic contaminants (those resulting 

from human activity) are deposited from the atmosphere and discharged from point sources such as sanitary, combined, and storm sewers and from industrial 

facilities. Contaminants also originate as runoff from 

nonpoint sources such as urban, suburban, agricul-
2 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

tural, and silvicultural areas. Areal distribution, concentrations, and bioavailability of contaminants in 

streambed and lakebed sediments are key issues in the 

Lake Erie–Lake Saint Clair Drainages. Although 

numerous studies of contaminants in aquatic sediments have been done in the Lake Erie–Lake Saint 

Clair Drainages, few studies have assessed how these 

contaminants vary from place to place and under different environmental conditions.

Streambed and lakebed sediments of the Lake 

Erie–Lake Saint Clair Drainages provide habitat for 

many aquatic organisms, but they also serve as a major 

repository for persistent and toxic chemicals that have 

been released into the environment or occur naturally. 

Since the early 1970’s, people have been concerned 

about elevated concentrations of various synthetic 

organic compounds and trace metals in these streambed and lakebed sediments. Evidence from laboratory tests shows that contaminated aquatic sediments 

can reduce or eliminate benthic (bottom-dwelling) 

species of recreational, commercial, or ecological 

importance or affect the food supply required to sustain fish populations (U.S. Environmental Protection 

Agency, 1997a). Furthermore, bed-sediment contaminants can accumulate in the tissue of benthic organisms, causing health risks to predatory fish, wildlife, 

and human consumers as the contaminants move 

through the food chain.

The Great Lakes Water Quality Agreement 

(GLWQA) calls for governments throughout the Great 

Lakes Basin to reduce and eliminate persistent bioaccumulative and toxic substances. The Lake Erie Lakewide Management Plan (LaMP) and 11 other 

Remedial Action Plans (RAP’s) are programs that 

Canada and the United States are undertaking as part 

of an ongoing commitment to carry out the GLWQA 

(Daher, 1998). The committees of citizens and naturalresource managers comprising the LaMP’s and RAP’s 

have been charged with identifying, remediating, and 

restoring beneficial uses of the lake where impairments to these uses have been identified. Key findings 

from the study of the Lake Erie–Lake Saint Clair 

Drainages will provide needed information to these 

and other water-resources-management programs. 

Fourteen highly desirable human uses of aquatic 

resources in the Great Lakes Basin, termed “beneficial 

uses,” were identified by the International Joint Commission (IJC). As many as 9 of the 14 beneficial uses 

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE ERIE

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

Grand

Black

River

R

R

Tonawanda R

Belle

Niagara R

Buffalo

R

R

Clinton

R

C

Creek

att a raugus

R

St. ClairThames

Rouge River

Huron

R

Rive

R

r

Detroit

Conneaut

Raisin

Ash tabula

R Cre

R

ek

River

Cuyahoga

Tiffin R

River

Black

Grand

Portage River Maumee

R

St. Joseph

R

B la n chard River

St. Marys River

River

R

Sandusky

Auglaize

NIAGARA FALLS

ERIE

DETROIT

MONROE

CLEVELAND

FINDLAY

FORT WAYNE

SANDUSKY

ANN

ARBOR

LIMA

TOLEDO

AKRON

LONDON

HAMILTON

KITCHENER

TORONTO

BUFFALO

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Ohio

Penn.

N.Y.

Ind.

Mich.

Canada

Figure 1. Location of Lake Erie-Lake Saint Clair Drainages study unit, principal streams, and major cities.
Introduction 3

are potentially impaired by sediment contamination in 

the Lake Erie–Lake Saint Clair Drainages. The possible consequences of these impairments are degraded 

fish populations, loss of fish habitat, fish tumors or 

other deformities, bird or animal deformities or reproductive problems, degradation of bottom-dwelling 

invertebrates (benthos), fish- and wildlife-consumption restrictions, tainting of fish and wildlife flavor, 

and restrictions on dredging activities. The impairment 

potential of populations of benthos is specifically 

addressed by this report. 

A total of 37 bed-sediment contaminants of concern have been identified in the Lake Erie Basin (table 

1). The list is inclusive of most contaminants identified by Federal, state, provincial, binational, and other 

organizations who are involved in water-quality programs in the Great Lakes Basin. For example, the list 

(table 1) includes the LaMP “critical pollutants,” 

PCB’s (polychlorinated biphenyls), mercury, U.S. 

Environmental Protection Agency (USEPA) “bioaccumulative” chemicals of concern, the Canada-Ontario 

Agreement Tier 1 and Tier 2 chemicals, and three 

additional trace metals (zinc, copper, and lead) identified by the Detroit River RAP. Of the 37 bed-sediment 

contaminants identified in table 1, available data for 

only 20 were sufficient for analysis.

Table 1. Organic compounds and trace metals in bed sediment identified by the Lake Erie Lakewide Management Plan (LaMP) 

as chemical contaminants of concern in the Lake Erie Basin, United States and Canada.

[Contaminants with a* are degradation products; those shown in italics have been identified as “critical pollutants” by the Lake Erie LaMP or have 

been shown to impair beneficial uses of Lake Erie]

_____________________________________________________________________________________

Contaminant(s) Common sources or uses _____________________________________________________________________________________

Organochlorine insecticides or biocides

Chlordane total 1,3,4,5 Historical use for control of mosquitoes, ants, 

 γ chlordane cockroaches, and termites. Chlordane was used

 α chlordane on agricultural crops, such as corn, potatoes, and

*Cis nonachlor tomatoes, as well as on home gardens, to control

*Trans nonachlor soil insects (Shelton, 1990). Canceled in 1988.

DDT total1,2,3,4,5

*DDD Widespread use as a contact insecticide. 

*DDE Canceled in 1972 (Gessner and Griswold, 1978).

Dieldrin1,3,4,5 Used to control insect pests on corn and citrus fruits.

Canceled in 1989 (Binational Toxic Strategy, 1998).

Toxaphene2,3,4,5 Turpentine, fish control, row crops. canceled in 1982.

Mirex2,3,4,5 Historical use for fire ants and as a flame retardant.

*Photomirex Canceled in 1977. May still be used as a color-enhancing 

agent in fireworks (Binational Toxic Strategy, 1998).

Ηexachlorocyclohexane, total3 Agricultural and topical insecticides used in the United States to

α-Hexachlorocyclohexane control flies, cockroaches, aphids, and boll weevils.

β-Hexachlorocyclohexane Lindane (the gamma isomer of hexachlorocyclohexane)

δ-Hexachlorocyclohexane is registered for commercial and home use. Lindane is an

γ-Hexachlorocyclohexane (Lindane3, 5) active ingredient in several head-lice shampoos and is used to treat seeds.

Hexachlorobenzene3,4 Wood preservatives, fluorocarbons, tetrachloroethylene.

Industrial organochlorine compounds or byproducts

PCB and congeners1,2,3,4,5 Transformers, lubricants, hydraulic fluids. Restricted in 1979.

Dioxin (2,3,7,8 TCDD)3,4,5 Paper production; waste, coal, and automobile combustion.
4 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Purpose and Scope

The purposes of this report are to (1) describe the areal 

distribution and concentrations of contaminants of 

concern in streambed and selected lakebed sediments 

in the Lake Erie–Lake Saint Clair Drainages, (2) compare these bed-sediment contaminant concentrations to 

guidelines that indicate concentrations either acutely 

or chronically toxic to aquatic macroinvertebrates, and 

(3) compare the extent and magnitude of contamination within Areas of Concern (AOC’s) to other areas. 

AOC’s are defined as the 12 specific geographic areas 

in the Lake Erie–Lake Saint Clair Drainages that have 

been identified as Areas of Concern by the International Joint Commission in the 1987 Revisions to 

GLWQA of 1972 (International Joint Commission, 

1987; see fig. 25). 

Accomplishing these objectives required the 

merging of four large databases that covered parts of 

the Lake Erie–Lake Saint Clair Drainages: the 

National Sediment Inventory (NSI), Ohio Sediment 

Data Inventory (OSI), USEPA Fully Integrated Environmental Locational Decision Support system 

(FIELDS) database, and the USGS-NAWQA sediment 

data. Only those bed-sediment samples collected from 

1990 to 1997 (in the top 5 in. of sediment) in the 

United States part of the Lake Erie–Lake Saint Clair 

Drainages were evaluated to reflect recent U.S. conditions. The location and concentration range of selected 

contaminants of concern are mapped, and each contaminant is discussed with regard to its toxicity to 

aquatic macro-invertebrates according to three 

regional bed-sediment-quality guidelines (Persaud and 

Table 1. Organic compounds and trace metals in bed sediment identified by the Lake Erie Lakewide Management Plan (LaMP) 

as chemical contaminants of concern in the Lake Erie Basin, United States and Canada.–Continued

Polycyclic aromatic hydrocarbons

3,4

PAH’s, total (expressed as a sum of 16 compounds)

Anthracene From incomplete combustion of coal, oil, gas, and coking 

Benz[a]anthracene byproducts, waste incineration, wood and tobacco 

Benzo[a]pyrene smoke, forest fires, automotive exhaust, tars and

Benzo[b]flouranthene tar products. PAH’s are usually found in smoke and 

Benzo[k]flouranthene soot. PAH’s are produced in petroleum refining and 

Chrysene kerosene processing. PAH’s are found in runoff containDinitropyrene ing greases and oils, and are a potential roadbed and 

Perylene asphalt leachate (Verschueren, 1977).

Phenanthrene

Trace metals

Arsenic5 Orchard and forest sprays, natural occurring in some areas.

Cadmium3,4 Batteries, ceramics, metal coatings, sludge disposal.

Copper5 Electrical industry, plumbing, fungicides and algal control.

Lead3,4,5 Leaded gasoline, batteries, plumbing, pigments in paint.

Mercury1,2,3,4,5 Coal and waste combustion, batteries, paint, industrial

uses.

Tributyl tin3,4 Antifouling paint.

Zinc 5 Galvanizing, dyes, paints, pesticides, and fertilizers.

__________________________________________________________________________________

1

 Lake Erie critical pollutant identified by Lake Erie LaMP in 1994. 

2 Great Lakes Initiative Bioaccumulative Chemical of Concern (BCC). 

3

 Canada-Ontario Agreement (COA) tier 1 or tier 2 contaminant. 

4

 Binational Toxics Strategy contaminant. 

5

 Contaminant identified by the International Joint Commission or in Remedial Action Plans (RAP’s)

Contaminant(s) Common sources or uses
Purpose and Scope 5

others, 1993; Ingersoll and others, 1996; Smith and 

others, 1996). 

Background

The Lake Erie–Lake Saint Clair Drainages (fig. 1) is a 

22,300-mi2 area in the United States, approximately 

two-thirds of the total 30,140-mi2 area of the Lake Erie 

Basin in the United States and Canada. From west to 

east, this includes parts of northeastern Indiana (6 percent), southeastern Michigan (27 percent), northern 

Ohio (62 percent), and areas in northwestern Pennsylvania and western New York (5 percent). Drainage for 

the study unit begins at the outflow of Lake Huron and 

includes all the tributaries draining to the St. Clair 

River, Lake Saint Clair, the Detroit River, and Lake 

Erie, the 11th-largest freshwater lake in the world. The 

study unit ends at the Niagara River, the outflow of 

Lake Erie. Principal rivers in the study unit are the 

Black, Belle, Clinton, River Rouge, Huron, and River 

Raisin in Michigan; the Maumee River and its tributaries (St. Joseph, St. Marys, Tiffin, Auglaize, Ottawa, 

and Blanchard) in Ohio, Michigan, and Indiana; the 

Portage, Sandusky, Black, Cuyahoga, Grand, and Ashtabula Rivers in Ohio; Conneaut Creek in Ohio and 

Pennsylvania; and Cattaraugus Creek, the Buffalo 

River, and Tonawanda Creek in western New York. 

Population density and growth in the Lake Erie–

Lake Saint Clair Drainages are among the highest in 

the Great Lakes area. About 40 percent of the total 

population of the Great Lakes Basin lives in the Lake 

Erie–Lake Saint Clair Drainages. The U.S. population 

in 1990 was 9.76 million: 3.93 million in Ohio, 4.64 

million in Michigan, 0.34 million in Indiana, 0.23 million in Pennsylvania, and 0.62 million in New York 

(Casey and others, 1997). Land use is a mix of agriculture, urban, and forest areas (Casey and others, 1997; 

fig. 2). Agriculture makes up 74.8 percent of the total 

Basin area, with croplands and pasture as the predominant types. Orchards and vineyards are located along 

the Lake Erie shoreline in Ohio, Pennsylvania, and 

New York because of the moderating effect of the lake 

on the local climate. Urban land use accounts for 11.2 

percent of the Basin area, with residential (6.7 percent) 

predominating and commercial (1.5 percent), transportation (0.9 percent), industrial (0.8 percent) and other 

mixed urban land (1.3 percent) making up the remainder. The largest cities are near the Lake. Forested areas 

constitute 10.5 percent of the Basin area, whereas 

water, wetlands, and barren land constitute less than 

4.0 percent of the Basin area (Casey and others, 1997). 

Detailed information on the environmental and hydrologic setting of the Lake Erie–Lake Saint Clair Basin 

is given in Casey and others (1997).

Study Design

Surficial bed-sediment data from streams across the 

Lake Erie–Lake Saint Clair Drainages and selected 

sites in Lakes St. Clair and Erie have been evaluated 

for this report in an effort to provide a better understanding of recent U.S. conditions and to identify areas 

where new or additional aquatic bed-sediment data are 

needed. The classes of compounds investigated in this 

report were organochlorine pesticides, total polychlorinated biphenyls (PCB’s), polycyclic aromatic hydrocarbons (PAH’s), and trace metals.

Throughout the Lake Erie Basin, aquatic bedsediment samples have been collected and analyzed, 

and the data have been stored in several large databases. Data have been collected by many public-sector 

agencies; the USEPA, U.S. Army Corps of Engineers 

(USACE), U.S. Fish and Wildlife Service (USFWS), 

USGS, Ontario Ministry of the Environment (OME), 

Ohio EPA, Michigan Department of Natural 

Resources (MDNR), more recently named Michigan 

Department of Environmental Quality (MDEQ), and 

universities, and their consultants (Fox, 1994). Most of 

these data were found in four national and regional 

databases, the NSI, OSI, USEPA-FIELDS, and 

NAWQA. These databases include chemical and physical data for aquatic bed-sediment samples from tributaries, connecting channels, harbors, and Lake Erie 

and Lake Saint Clair (proper) collected in the United 

States and Canada. Data consist of information on 

sampling location, sampling method, analytical 

method, concentration, sample weight, core depth, 

grain-size information, and percent total organic carbon (TOC) for a large list of contaminants in samples 

collected from the early 1970’s to 1997. For this 

report, only recent data (1990-97) collected from the 

United States part of the Lake Erie Basin were analyzed (fig. 3). Only contaminants of concern with both 

sufficient data for analysis and existing bed-sediment 

quality guidelines were included in the report.
Purpose and Scope 6

OHIO

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PENNSYLVANIA

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LAKE ERIE

LAKE

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LAKE ONTARIO

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ST. CLAIR

86 ̊ 85 ̊ 83 ̊ 80 ̊ 79 ̊

40 ̊

42 ̊

43 ̊

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41 ̊

20 40 60 MILES

0 20 40 60 KILOMETERS

0

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PENNSYLVANIA

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PENNSYLVANIA

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ONTARIO

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EXPLANATION

LAND USE/LAND COVER CLASSES

Agriculture

Urban

Forest

Open water

Wetlands

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Agriculture

(74.7%)

Forest

(10.6%)

Urban

(11.4%)

Wetland

(1.2%)

Open water

(2.1%)

OHIO

MICHIGAN

INDIANA

OHIO

PENNSYLVANIA

NEW YORK

PENNSYLV

OHIO

ANIA

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE ERIE

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

86 ̊ 85 ̊ 83 ̊ 80 ̊ 79 ̊

40 ̊

42 ̊

43 ̊

44 ̊ 84 ̊ 82 ̊ 81 ̊ 78 ̊

41 ̊

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Figure 2. Landuse/land cover in the Lake Erie-Lake Saint Clair Drainages, 1992.

Figure 3. Location of bed-sediment samples analyzed for potential contaminants in the Lake Erie-Lake Saint 

Clair Drainages, 1990-97.
Study Methods 7

National Sediment Inventory (NSI). In 1993, the 

USEPA began developing the NSI. The scope of the 

NSI database was to review readily available sediment-chemistry data and evaluate the extent and 

severity of bed-sediment contamination throughout the 

United States. Data incorporated into the NSI database 

from the Great Lakes area include contributions from 

the USEPA’s Storage and Retrieval System 

(STORET), USACE, USGS, USEPA National Bioaccumulation Study, USEPA Great Lakes Sediment 

Inventory, USEPA Environmental Monitoring and 

Assessment Program (EMAP), state resource agencies, universities, and consultants. Approximately 

two-thirds of the sampling stations in NSI were 

obtained from STORET.

Ohio Sediment Inventory (OSI). The Ohio EPA’s Division of Surface Water maintains two sediment databases: the OSI database and the SED BIO data- base. 

The OSI is the larger of the two, and it currently 

(2000) contains organic and trace-element data collected from 1972 to 1997 by Ohio EPA or their contractors from more than 1,000 sites throughout Ohio. 

The SED BIO database contains Ohio EPA bedsediment data for trace metals collected by the Ohio 

EPA’s Ecological Assessment Unit. Both databases 

include fields for database sample number, project station, sample date, time of sample, sampling organization, collection device, site name, river code, river 

mile, and latitude and longitude. 

Fully Integrated Environmental Locational Decision 

Support system (FIELDS). The USEPA FIELDS database contains data from (1) USACE reports for the 

Detroit River, Clinton River, River Rouge, Huron 

River, and River Raisin for the period 1970–93, (2) 

USACE sediment sampling digital files for the River 

Rouge, (3) MDNR Surface Water Quality Division’s 

digital sediment data for the Detroit River, and (4) 

Ontario Ministry of Environment (OME) Detroit 

River Study digital bed-sediment data collected in 

1991.

FIELDS is no longer housed and maintained by 

USEPA-Region 5. The FIELDS program has shifted 

focus from database aggegates to GIS visualization 

and interpretation models. The database currently contains data from approximately 2,380 sites, most of 

which are in southeastern Michigan.

National Water-Quality Assessment Program 

(NAWQA). The NAWQA bed-sediment database 

includes information on contaminants in aquatic bed 

sediment at 15 environmentally representative sites on 

major streams in the Lake Erie–Lake Saint Clair 

Drainages. Digital data includes information on grain 

size, percent total organic carbon, and concentrations 

of total PCB’s, 30 organochlorine pesticides, 16 polyaromatic hydrocarbons, 48 semivolatile organic compounds, and 44 elements. 

Study Methods

Screening procedures applied to the data before 

analysis are described in this section. Further details 

about the screening criteria used to evaluate whether 

the data were suitable to include in the analyses made 

for this report (methods and reporting limits) are contained in Appendix A. 

Data from each of the four databases were combined into a single data set for statistical analysis. 

Screening criteria were applied in an attempt to provide the degree of consistency necessary to combine, 

analyze, and interpret these data. Although these data 

were collected for different purposes by different 

agencies, the overall purpose of the studies from 

which these data arise was to assess aquatic bed-sediment contamination for toxic, persistent, and bioaccumulative contaminants. Because of that common 

objective, most of the data were collected and analyzed by use of accepted and published methods for 

soils and (or) streambed sediments. Sample analytical 

results were produced under the guidelines contained 

in each project’s QA/QC (quality assurance and quality control) Plans. Only those project data meeting the 

screening criteria were accepted for further statistical 

analysis and interpretation.

Sampling Agencies and Analyzing Laboratories

A total of seven public agencies collected and provided the data used in this report. The seven agencies 

included three Federal, one regional, and three state 

agencies. The Federal agencies were the USEPA 

Region 5, the USGS, and the USACE. The state agencies were the Ohio EPA, the MDNR, and the New 

York State Department of Environmental Conservation (DEC). The regional (multicounty) agency was 

the Rouge Program Office (RPO).

A total of 15 laboratories analyzed and reported 

sample results, 5 in the public sector and 10 in the private sector. Of the five public-sector laboratories, two 

were Federal and three were state laboratories. The 

public-sector laboratories were the USGS National 
8 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Water Quality Laboratory and the USACE Ohio River 

Division Laboratory. The three state laboratories were 

the Ohio EPA Division of Environmental Services 

Laboratory, the MDNR State Water Laboratory, and 

the New York State Laboratory of Health. Private-sector laboratories included Ecology and Environment, 

Inc., National Environmental Testing, Inc., Betz Laboratories, Aquatec Laboratories, Metcalf and Eddy, 

Inc., Thermo Analytical Inc., Ross Laboratory, Inc., 

Heidelberg College Water Quality Laboratory, and 

three other laboratories identified as “Other” by the 

Ohio EPA. 

Other Screening Criteria

In all, data from 823 sample sites were selected for 

analysis from the 2,938 Lake Erie–Lake Saint Clair 

Drainages sites listed in the USEPA NSI, Ohio EPA’s 

OSI, FIELDS, and NAWQA sediment databases (fig. 

3). Data were selected or eliminated on the basis of 

sample location, date, depth, and replication for each 

of the databases, as follows:

Location. Data analysis was limited to the U.S. side of 

the Lake Erie–Lake Saint Clair Drainages. Samples 

collected at contaminated sites such as landfills or 

known hazardous-waste disposal sites were excluded 

in an effort to characterize only ambient stream or lake 

conditions. Sediment data from sites in lagoons, 

ponds, reservoirs, or inland lakes were not used in the 

analysis. The vast majority of sites are stream sites, 

but several sites on the margin or within Lakes St. 

Clair and Erie met the location criteria (fig. 3).

Date. In an effort to characterize recently deposited 

sediments, only samples collected from calendar year 

1990 through 1997 were included for analyses. At a 

few locations, a site may have been revisited over the 

8-year period. In these instances, the most recent sample was used in the analysis, and the previous sample 

results were excluded. 

Depth. In order to characterize recently deposited sediments, only the top 5 in. of surficial bed sediments of 

streams were included in the analysis. Common methods for sampling sediment usually involve either core 

or grab samples. Core samples include material (sediment) from a wide range of depths, whereas grab samples usually represent the top 5 in. or less of material.

Replication. Field duplicate and field replicate samples were not included in the data set. These additional 

samples are used primarily for quality control or quality assurance of field or laboratory methods of sample 

collection, handling, and analysis. They might include 

additional samples collected at the same location and 

time (replicates) or subsamples split from the original 

(duplicates). The NSI contained sediment information 

for 955 sites in the Lake Erie–Lake Saint Clair Drainages. After screening against the data-selection criteria, only 0.5 percent of the data in NSI were used in 

the analysis. The most limiting factor for NSI site 

selection was the year of sampling; only 3 percent of 

the samples were collected during or after 1990. NSI 

data in this report include only three sites in the New 

York part of the Lake Erie–Lake Saint Clair Drainages.

The Ohio EPA’s OSI database contained sediment information for 666 sites in the Lake Erie–Lake 

Saint Clair Drainages. After screening, only 347 sites 

in OSI database were used in the analysis. Approximately 50 percent of the data met the criteria for being 

sampled between 1990 and 1997. A few sites represented samples collected in lagoons, ponds, or small 

lakes, and these sites were excluded from the analysis. 

Multiple samples collected from the same location on 

the same date were excluded. These additional samples were assumed to be replicates. 

The FIELDS database contained sediment information for 1,302 sites in the Lake Erie–Lake Saint 

Clair Drainages. After screening, only 455 sites in 

FIELDS were used in the analysis. As much as 55 percent of FIELDS data were excluded because samples 

had been collected before 1990. Any samples with 

qualifiers or comments indicating that they were 

extraction replicates were excluded. Also, in any case 

where a sample was collected at the same location on 

the same day, only data from the first occurrence was 

selected. Some sampling projects within FIELDS used 

grab samples, whereas others used core samples. Only 

samples meeting the requirements of being collected 

from the top 5 in. of the surficial sediments were used 

in the analysis. If a depth was not specified for a core 

sample, data from that sample were not used in the 

analysis. If a grab-sample depth was not recorded, the 

sample was assumed to be only a few inches deep and 

was used in the analysis. Because of the uncertainty of 

sample depth, limitation based on depth was the most 

restrictive requirement in selecting data from FIELDS.

The NAWQA data set contained sediment information for 15 sites in the Lake Erie–Lake Saint Clair 

Drainages. The NAWQA samples were collected in 

1996 and 1997. Sediment samples collected by 

NAWQA investigators were obtained with a hand-held 

grab sampler in wadeable areas. Each sample was col-
Study Methods 9

lected from the top 2 to 3 inches of the sediment 

deposit. Replicates of field samples were not included 

in the data set. All 15 sample results were used in this 

analysis.

Sediment-Quality Guidelines Selected for Comparison 

With Site Data

Because of the many complex factors involved in bioaccumulation, contaminant concentrations in streambed sediments cannot be used as direct measures of 

the potential for contaminants to cause adverse effects 

on human health. It is possible, however, to relate sediment-contaminant concentrations to the potential for 

adverse effects on the health of aquatic organisms that 

live in or on these sediments. Although much still 

needs to be understood with respect to the behavior, 

bioavailability, and toxicity of contaminants in the 

aquatic bed sediments of the Lake Erie–Lake Saint 

Clair Drainages, recent progress in developing bedsediment-quality guidelines for aquatic life has greatly 

helped environmental managers to make regulatory 

and cleanup decisions that are based on the best scientific information available.

Numerical sediment-quality guidelines are useful tools for assessing sediment quality. Such guidelines have been developed by various jurisdictions 

around North America using many approaches (U.S. 

Environmental Protection Agency, 1997a). Many of 

the studies resulting in guidelines deal with the concentrations of individual contaminants in sediments at 

which toxicity is rarely and (or) frequently observed; 

however, most deal with marine and estuarine sediments (Long and Morgan, 1991). Only a few studies 

have been published on Great Lakes (freshwater) sediments (Persaud and others, 1993; Ingersoll and others, 

1996; Smith and others, 1996).

This study compares the concentrations of contaminants of concern detected in bed-sediment samples to three freshwater bed-sediment-quality 

guidelines used in the Great Lakes area (table 2). 

These are (1) Ontario Ministry of Environment (OME) 

guidelines for the protection and management of 

Canadian freshwater sediments, (2) USEPA guidelines 

for Great Lakes sediments, and (3) Environment Canada and the Great Lakes (EC&GL) guidelines for ecosystems throughout Canada and the Great Lakes 

Drainages (Graphical comparisons, referred to later in 

this report, are in Appendix B. Information on the 

development of the Canadian and U.S. guidelines is 

given in Appendix C.). These guidelines can serve 

only as screening tools for streambed sediments in 

freshwater streams, and they do not replace the need 

for toxicity testing or aquatic-community assessments 

to determine specific adverse effects on aquatic organisms endemic to a particular site. Evaluation of fish 

and benthic communities at a site provides an indication of the effect of contaminant biomagnification up 

the food chain and of the subtle effects of contaminants on reproduction, growth, and behavior. Numerical sediment-quality assessment values used for 

comparisons in this report are listed in table 2.

Guidelines Selected

For this report, the Threshold Effect Levels (TEL’s) 

and Probable Effect Levels (PEL’s) developed by 

Smith and others (1996) for Environment Canada and 

the Great Lakes (EC&GL) were most frequently used 

to assess the possible effects of contaminants in surficial bed sediments on populations of aquatic macroinvertebrates. These sediment quality criteria were 

selected over the other two available guidelines (table 

2) because they contained guidelines for more organochlorine insecticides, PCB’s, PAH’s, and trace metals than the other two. In addition, Smith and others’ 

criteria (1996) are considered to be the most sensitive 

of the three sets of guidelines; therefore, using them 

represents the most conservative approach to protecting sediment quality. 

If bed-sediment-quality guidelines indicating 

the adverse biological effects of contaminants of concern were not available from Smith and others (1996), 

TEL’s and PEL’s from Ingersoll and others (1996) 

were used. These two sets of guidelines were in 

greater agreement about the concentrations of contaminants likely to cause various degrees of adverse 

effects in benthic communities than either set was in 

comparison to Persaud and others (1993). In addition, 

the sediment-quality guideline concentrations proposed by Ingersoll and others (1996) and Smith and 

others (1996) were almost always lower than those 

proposed by Persaud and others (1993). 

Lowest Effect Levels (LEL’s) and Severe Effect 

Levels (SEL’s) from Persaud and others (1993) were 

used only if guidelines for a constituent of concern 

were not available from either of the other two references. However, for SEL nonpolar organic compound 

values listed in table 2, the conservative approach, as 

suggested by Smith and others (1996), was taken 

(which assumed a 1 percent total organic carbon 

(TOC) sample value). This approach seemed appropri-
10 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

ate for the Lake Erie– Lake Saint Clair Drainages, 

where TOC values averaged between 1-2 percent. 

Statistical and Graphical Methods

Areal-distribution maps are used to illustrate the 

range of concentrations of contaminants reported for 

bottom sediments of streams, rivers, harbors, and 

shorelines in the Lake Erie–Lake Saint Clair Drainages. The ranges shown on the maps were selected to 

compare sediment concentrations relative to detection 

limits and to sediment-quality guidelines reported by 

Persaud and others (1993), Ingersoll and others 

(1996), and Smith and others (1996). Areal-distribution maps were generated for each contaminant of 

concern (figs. 4–23). Each map shows the location at 

which that specific contaminant was reported and its 

Table 2. Selected guidelines for chemical concentrations in freshwater bed sediment that have been observed or predicted to be associated 

with adverse effects on aquatic biota

[Sediment concentrations are in milligrams per kilogram dry weight; - -, no guidelines available; (), guideline used in contaminant maps--figures 4-23 of this 

report.]

 1 Persaud and others, 1993.

 2 Ingersoll and others, 1996. 

 3 Smith and others, 1996. 4 Severe Effect Level values for nonpolar organic compounds are based on an assumed 1 percent total organic carbon in the sample.

Chemical constituent

Ontario Ministry of the

Environment 

Provincial Sediment Quality

Guidelines1

U. S. Environmental Protection 

Agency

Great Lakes Sediment Effect 

Concentrations2

Environment Canada 

and Great Lakes

Sediment Quality Assessment 

Values3

Lowest Effect 

Level

Severe Effect 

Level4

Threshold Effect 

Level

Probable Effect 

Level

Threshold Effect 

Level

Probable Effect 

Level

Organochlorine insecticides or biocides

Chlordane, total 0.007 0.06 - - - - (0.0045) (0.0089)

DDT, total .007 .12 - - - - (.0070) (4.45)

Dieldrin plus aldrin .002 .910 - - - - (.00285) (0.00667)

Hexachlorobenzene (.02) (.24) - - - - - - - -

Hexachlorocyclohexane, total (.003) (.12) - - - - - - - -

Lindane - - - - - - - - (.00094) (.00138)

Mirex, total (.007) (1.30) - - - - - - - -

Industrial organochlorine compounds

PCB’s, total 0.07 5.3 0.032 0.24 (0.0341) (0.277)

Polycyclic aromatic hydrocarbons

Anthracene 0.22 3.70 (0.010) (0.17) - - - -

Benz[a]anthracene .32 14.8 .016 .28 (0.0317) (.385)

Benzo[a]pyrene .37 14.4 .032 .32 (.0319) (.782)

Chrysene .34 4.6 .027 .41 (.0571) (.862)

Phenanthrene .56 9.5 .019 .41 (.0419) (.515)

PAH’s (total) 4.0 100.0 (.260) (3.4) - - - -

Trace metals

Arsenic 6 33 11 48 (5.9) (17)

Cadmium 0.6 10 0.58 3.2 (.596) (3.53)

Copper 16 110 28 100 (35.7) (197)

Lead 31 250 37 82 (35) (91.3)

Mercury .2 2 - - - - (.174) (.486)

Zinc 120 820 98 540 (123) (315)
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 11

concentration relative to bed-sediment guidelines. 

Maps were created by use of a geographic information 

system (GIS) plotting program linked with the data 

sets selected for the study. 

Probability plots, which are plots of the probability of a sample concentration being greater than a 

given value, were constructed for each contaminant 

(Appendix B). A probability plot is a type of quantile 

plot that uses a plotting position. The plotting position 

is subsequently multiplied by 100 and displayed as a 

percentile on the x-axis of the graph while the concentration is displayed on the y-axis. This method is a 

robust procedure and is recommended for analyzing 

and displaying data sets that are characterized by multiple detection limits (Helsel and Hirsch, 1995, p. 362-

364). Data analyzed for this report are characterized 

by multiple detection limits. By use of probability 

plots, the data can be displayed as the percent probability of occurrence (Helsel and Hirsch, 1995, p. 29). 

The probability plots show samples with no detected 

concentrations, samples with detected concentrations, 

concentration ranges, and contaminant guidelines. The 

percent frequency of detection was computed as the 

fraction of total samples reported with results above 

the detection limit times 100.

Star diagrams (figs. 26-27) were used to display 

and summarize contaminant-concentration data on 

multiple axes. One observation, either the 75th-or 

90th-percentile concentration, was represented by a 

point on an axis of the multiple-axis star, and these 

points are connected by line segments. Star diagrams 

used for this report are six-pointed, so that data for six 

contaminants can be shown on one star. Unusual 

observations will stand out as a noticeable difference 

in the shape from other stars (Helsel and Hirsch, 1995, 

p. 53).

Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments

Twenty contaminants of concern found in surficial bed 

sediments of surface waters in the Lake Erie–Lake 

Saint Clair Drainages are discussed in this section. 

These 20 contaminants are those for which sufficient 

data were available for analysis and for which bedsediment-quality guidelines also are available. They 

are among four chemical classes: organochlorine pesticides, PCB’s, PAH’s, and trace metals. The number 

of samples collected for analysis of each chemical 

constituent, the number of samples with detections, 

and the range of the detected concentrations used in 

this report, are listed in table 3. Maps showing the spatial distribution and concentration range for each of 

the 20 contaminants of concern are included in the discussion of the four chemical classes (figs. 4-23), and 

contaminant probability-distribution plots are shown 

in Appendix B.

Stream reaches for which data are inadequate or 

unavailable include the following: 

Michigan--main stems of the Black River, Bell 

River, Huron River, and upper River Raisin; 

Indiana--lower St. Mary’s River and most of the 

St. Joseph River; 

Ohio--upper Sandusky River, and upper Grand 

River; and 

New York--Cattaraugus Creek, the Buffalo River 

and its tributaries, and Tonawanda Creek. For the most 

part, recent bed-sediment data were not electronically 

available for Pennsylvania and New York.

Organochlorine Compounds

Organochlorine compounds analyzed for this report 

are organochlorine pesticides and polychlorinated 

biphenyls. Many organochlorine pesticides are no 

longer manufactured or sold for use in the United 

States or Canada because of environmental and 

human-health concerns. An exception is lindane. 

Organochlorine pesticides and PCB’s are still manufactured and used in certain parts of the world. Organochlorine compounds generally are characterized by 

their great persistence in the environment and are considered highly toxic to fishes and lower aquatic organisms. These compounds have a high affinity for lipids 

(fatty tissue), resulting in their biomagnification 

within organisms. Chlorinated organic compounds are 

hydrophobic; they tend to absorb to organic carbon 

and other fine particles in suspended and bed sediments. Because of this behavior, these compounds can 

be present in sediments in concentrations that are 

orders of magnitude greater than those in water. Therefore, sediments can provide a mechanism by which 

environmentally persistent organochlorine compounds 

remain in a surface-water system many years after 

their initial input (Smith and others, 1988).

Total chlordane (sum of chlordane, oxychlordane, cis-nonachlor, and trans-nonachlor). Chlordane 

is a wide-spectrum insecticide that was introduced in 

1947 for urban and agricultural uses. Chlordane consists of gamma and alpha isomers and technical chlordane. Its degradates are oxychlordane, cis-nonachlor,
12 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

and trans-nonachlor. Chlordane has been used for the 

control of mosquitoes, cockroaches, ants, and termites. 

Until April 1976, chlordane was used on agricultural 

crops such as corn, potatoes, and tomatoes, as well as 

home garden crops, to control soil insects (Shelton, 

1990). USEPA restricted its agricultural use in 1976 

and the canceled virtually all other uses in April 1988. 

Of the 371 bed-sediment samples analyzed for 

total chlordane, only 29 samples (7.82 percent) 

showed detectable concentrations. Of the 29 samples 

with chlordane detections, 4 sample concentrations 

ranged from the TEL to less than the PEL, 16 samples 

were from 1 to less than 10 times the PEL, and 2 sample concentrations ranged from 10 to less than 100 

times the PEL (figs. 4 and B1, table 3). Of the 342 

samples with no detections of chlordane, detection 

limits for less than half, 36 and 155 samples, were less 

than the TEL and PEL, respectively; thus, these samples were used for assessment purposes. Lower detection limits would have made the data more useful. 

The highest concentrations of chlordane in bed 

sediments were found in samples collected from 

1994–95 in Michigan in the Clinton River near the 

mouth and in Lake Saint Clair (fig. 4). At these locations, concentrations ranged from 0.10 to 0.12 mg/kg. 

These concentrations were 11.7 to 13.5 times the PEL. 

Other locations where concentrations of chlordane 

exceeded the PEL (listed in order of decreasing concentration) were as follows: the mouth of the Maumee 

River, Ohio; a tributary to the Ottawa River at Toledo, 

Ohio; a tributary to the Little Cuyahoga River near 

Akron, Ohio; tributaries to the lower Cuyahoga River 

near Cleveland, Ohio; the main stem of the Little 

Cuyahoga River, Ohio; the mouth of the Vermilion 

River, Ohio; and the mouth of the Ashtabula River, 

Ohio.

Total DDT (sum of isomers of DDT, DDD, DDE). 

DDT degrades to DDE and DDD, which also are toxic 

and highly resistant to further chemical decomposition. DDT and its isomers are the most permanent and 

durable of all contact insecticides because of their 

insolubility in water, their low vapor pressure, and 

their resistance to destruction by light and oxidation 

(Gessner, 1978).Widespread use of DDT began in 

1939, peaked in the 1960’s, continued until about 

1970, and greatly declined when use of DDT was canceled in 1972. 

Of the 409 bed-sediment samples analyzed for 

total DDT, 145 samples (35.4 percent) contained 

detectable concentrations. Of the 145 samples with 

detectable concentrations, 109 sample concentrations 

ranged from the TEL to less than the PEL, and 1 sample concentration was greater than the PEL (figs. 5 and 

B2, table 3). Of the 264 samples with no detections of 

total DDT, detection limits for 127 and 261 sample 

concentrations were less than the TEL and PEL, 

respectively; thus, these samples were used for assessment purposes. 

The highest concentration of total DDT was 

found in bed sediment at the mouth of the Clinton 

River, Michigan, in 1994 (fig. 5). At this location, the 

detected concentration was 22 mg/kg. This exceeded 

the PEL by 4.9 times. Other locations with elevated 

concentrations of total DDT were the Ottawa River 

and its tributaries at Toledo, Ohio and a small tributary 

near the mouth of the Maumee River, Ohio, Lake Saint 

Clair, and the main stem of the Clinton River, in Michigan. 

Total dieldrin (sum of dieldrin plus aldrin). Aldrin, which quickly transforms into dieldrin, is metabolically converted to dieldrin by aquatic organisms. Both 

chemicals were used primarily in agricultural areas to 

control insect pests, originally on corn and later on citrus fruits (U.S. Environmental Protection Agency, 

1993c). These substances also were used in urban 

areas for control of termites, cockroaches, and fire ants 

into the 1980’s. Dieldrin and aldrin were two of the 

most widely used chlorinated hydrocarbon pesticides 

prior to their cancellation for surface use in 1974. 

Most remaining aldrin products were canceled by 

1987, the last product being canceled in 1991 (Binational Toxic Strategy, 1998). 

Of the 407 bed-sediment samples analyzed for 

dieldrin plus aldrin, 45 samples (11.1 percent) showed 

detectable concentrations. Of the 45 samples with

detectable concentrations, 7 sample concentrations 

ranged from the TEL to less than the PEL, 12 sample 

concentrations were from 1 to less than 10 times the 

PEL, and 1 sample concentration was from 10 to less 

than 100 times the PEL (figs. 6 and B3, table 3). Of the 

362 samples with no detections of dieldrin plus aldrin, 

detection limits in 25 and 228 samples were less than 

the TEL and the PEL, respectively; thus, these samples were used for assessment purposes. 

The highest concentration of total dieldrin in 

aquatic bed sediment was found in a tributary to the 

Ottawa River at Toledo, Ohio, in 1993 (fig. 6). At this 

location, the detected dieldrin concentration was 0.102 

mg/kg. This concentration was 15.2 times the PEL. 

Other locations where concentrations of dieldrin
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 13

Table 3. Number of bed-sediment samples reported, number with detected values, and the number detected in relation to 

sediment-quality guidelines, Lake Erie–Lake Saint Clair Drainages, 1990–97

[TEL, Threshold Effect Level; PEL, Probable Effect Level; LEL, Lowest Effect Level; SEL, Severe Effect Level. Values and references for all 

effect levels are listed in table 2]

1, γ-hexachlorocyclohexane.

Contaminant Total 

Number of samples in category

With 

detected 

values

Less than 

the TEL

Equal to or 

greater 

than the 

TEL but 

less than 

the PEL

Equal to or 

greater 

than the 

PEL but 

less than 

10 times 

the PEL

Equal to or 

greater than 

10 times PEL 

but less than 

100 times the 

PEL

Equal to or 

greater 

than 100 

times the 

PEL

Chlordane, total 371 29 7 16 4 2 0

DDT, total 409 145 36 108 1 0 0

Dieldrin plus aldrin 407 45 25 7 12 1 0

Lindane1 404 11 4 2 4 1 0

PCB, total 683 223 3 67 91 35 27

PAH, total 414 231 36 78 83 30 4

Anthracene 392 76 4 26 30 13 3

Benz[a]anthracene 393 158 17 65 55 20 1

Benzo[a]pyrene 388 147 15 63 59 9 1

Chrysene 396 189 26 86 65 11 1

Phenanthrene 398 187 26 66 74 19 2

Arsenic 480 470 141 269 58 2 0

Cadmium 616 588 276 198 114 0 0

Copper 587 586 363 209 14 0 0

Lead 615 614 349 156 109 0 0

Mercury 465 309 195 59 51 4 0

Zinc 575 575 326 167 82 0 0

Less than 

LEL

Equal to or 

greater 

than the 

LEL but 

less than 

the SEL

Equal to or 

greater 

than the 

LEL but 

less than 

10 times 

the SEL

Equal to or 

greater than 

10 times SEL 

but less than 

100 times the 

SEL

Equal to or 

greater 

than 100 

times the 

SEL

Hexachlorobenzene 411 6 1 3 2 0 0

Hexachlorocyclohexane, total 407 45 21 24 0 0 0

Mirex, total 199 0 0 0 0 0 0
14 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLV

OHIO

ANIA

CANADA

NEW YORK

ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

TOTAL CHLORDANE CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.0045 mg/kg)

PEL - Probable Effect Level (0.0089 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK

ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

TOTAL DDT CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.007 mg/kg)

PEL - Probable Effect Level (4.45 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 4. Total chlordane concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 5. Total DDT concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 15

exceeded the PEL (listed in order of decreasing concentration) were the main stem of the Ottawa River at 

Toledo, Ohio; a tributary to the mouth of the Cuyahoga River, Ohio; and the lower main stem of the 

Huron River, Ohio.

Hexachlorobenzene. Hexachlorobenzene is 

used as a wood preservative, is used in production of 

aromatic fluorocarbons, and is a byproduct in the manufacturing of tetrachloroethylene (Verschueren, 1977). 

Of the 411 bed-sediment samples analyzed for 

hexachlorobenzene, 6 samples (1.46 percent) showed 

detectable concentrations. Only Persaud (1993) provides sediment-quality guidelines for hexachlorobenzene. Of the six samples with detectable 

hexachlorobenzene, the concentration in three samples 

ranged from the LEL to less than the SEL, none were 

in the range from 1 to less than 10 times the SEL, and 

2 sample concentrations ranged from 10 to less than 

100 times greater than the SEL (figs. 7 and B4, table 

3). Of the 405 samples with no detections of hexachlorobenzene, detection limits for 185 and 248 samples 

were less than the LEL the SEL, respectively; thus, 

these samples were used for assessment purposes.

The highest concentrations of hexachlorobenzene ranged from 4.9 to 5.9 mg/kg in bed sediment 

sampled at two sites in the lower Ashtabula River, 

Ohio, in 1993 (fig. 7). Concentrations were 20.4 to 

24.6 times the SEL of 0.24 mg/kg

Total hexachlorocyclohexane (sum of α, β, δ,

and γ isomers). Hexachlorocyclohexane and its isomers are agricultural and topical insecticides (Parker, 

1984). There are four forms of hexachlorocyclohexane: alpha, beta, delta, and gamma (α, β, δ, and γ isomers). 

Of the 407 bed-sediment samples analyzed for 

total hexachlorocyclohexane, 45 samples (11.1 percent) showed detectable concentrations. Only Persaud 

(1993) provides sediment-quality guidelines for total 

hexachlorocyclohexane. Of the 45 samples with 

detectable total hexachlorocyclohexane, 24 sample 

concentrations ranged from the LEL to less than the 

SEL (figs. 8 and B5, table 3). Of the 362 samples with 

no detections of hexachlorocyclohexane, detection 

limits for 60 and 296 samples were less than the LEL 

and the SEL, respectively; thus, these samples were 

used for assessment purposes. 

The highest concentration of hexachlorocyclohexane, 0.04 mg/kg, was found in a headwater tributary to the Clinton River, Michigan, in 1994 (fig. 8). 

This concentration was about 17 times the LEL. Other 

locations where concentrations exceeded the LEL 

(listed in order of decreasing concentration) were the 

lower Clinton River, near Detroit, Michigan; the 

Ottawa River at Toledo, Ohio; the upper Maumee 

River, Ohio; a headwater tributary to the Auglaize 

River, Ohio; a headwater tributary to the Tiffin River, 

Ohio; a headwater tributary to the River Rouge, Michigan; the main stem of the Blanchard River, Ohio; and 

the headwaters of the St. Marys River, Ohio.

Lindane (γ-hexachlorocyclohexane). Lindane 

(the gamma isomer of hexachlorocyclohexane) is an 

organochlorine insecticide registered for commercial 

and home use. It is an active ingredient in several prescription shampoos used for the elimination of head 

lice (Shelton, 1990). 

Of the 404 bed-sediment samples analyzed for 

lindane, only 11 samples (2.72 percent) showed 

detectable concentrations. Of the 11 samples with 

detections of lindane, 2 sample concentrations ranged 

from the TEL to less than the PEL, 4 sample concentrations ranged from the PEL to less than 10 times the 

PEL, and 1 sample concentration was from 10 to less 

than 100 times the PEL (figs. 9 and B6, table 3). Of the 

393 samples with no detections of lindane, the detection limits for 32 and 64 samples were less than the 

TEL and PEL; thus, these samples were used for 

assessment purposes. Lower detection limits could 

have made most of the data more useful.

The highest concentration of lindane, 0.04 mg/

kg, was found in the sediments of a headwater tributary to the Clinton River, Michigan, in 1994 (fig. 9). 

This concentration was more than 25 times the PEL. 

Other locations where concentrations of lindane 

exceeded the PEL (listed in order of decreasing concentration) were the upper Maumee River, Ohio; a 

headwater tributary to the Tiffin River, Ohio; a headwater tributary to the Auglaize River, Ohio; and the 

Ottawa River at Toledo, Ohio.

Total mirex (sum of mirex plus photomirex). The 

degradation product of mirex is photomirex. Mirex 

was used in the Great Lakes area in the 1960’s and 

1970’s, primarily as a fire-retardant additive under the 

trade name Dechlorane. Mirex may still be used as a 

color-enhancing agent in fireworks (Binational Toxic 

Strategy, 1998). Mirex was used extensively in the 

southeastern United States to control fire ants. All pesticide uses of mirex were canceled in 1977. 

Of the 199 bed-sediment samples analyzed for 

mirex, no detections were reported (figs. 10 and B7, 

table 3). Only Persaud (1993) provides a sedimentquality guidelines for mirex. Detection limits for a relatively large percentage, 139 and 199 samples, showed
16 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK

ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE ERIE

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

DIELDRIN CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.00285 mg/kg)

PEL - Probable Effect Level (0.00667 mg/kg)

86 ̊ 85 ̊ 83 ̊ 80 ̊ 79 ̊

40 ̊

42 ̊

43 ̊

44 ̊ 84 ̊ 82 ̊ 81 ̊ 78 ̊

41 ̊

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

HEXACHLOROBENZENE CONCENTRATIONS

Not detected; detection limit equal to

 or greater than LEL

Less than LEL

Equal to or greater than LEL and

less than SEL

Equal to or greater than SEL and

less than 10 times SEL

Equal to or greater than 10 times SEL

and less than 100 times the SEL

Aquatic effects (Persaud and others, 1993)

LEL - Lowest Effect Level (0.02 mg/kg)

SEL - Severe Effect Level (0.24 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 7. Hexachlorobenzene concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair 

Drainages, 1990–97.

Figure 6. Total dieldrin concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 17

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES LAKE ERIE

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

TOTAL HEXACHLOROCYCLOHEXANE

Not detected; detection limit equal to

 or greater than LEL

Less than LEL

Equal to or greater than LEL and

less than SEL

Aquatic effects (Persaud and others, 1993)

LEL - Lowest Effect Level (0.003 mg/kg)

SEL - Severe Effect Level (0.12 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Buffalo

Detroit

Erie

Cleveland Toledo

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLV

OHIO

ANIA

CANADA

NEW YORK

ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

LINDANE (γ-HEXACHLOROCYCLOHEXANE)

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.00094 mg/kg)

PEL - Probable Effect Level (0.00138 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 8. Total hexachlorocyclohexane concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint 

Clair Drainages, 1990–97.

Figure 9. Lindane (γ-hexachlorocyclohexane) concentrations in streambed and lakebed sediments, Lake Erie–Lake 

Saint Clair Drainages, 1990–97.
18 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

no detections but at detection limits that were less than 

the LEL and SEL, respectively; thus, these samples 

were used for assessment purposes. Spatial distribution of sites where mirex was sampled for is shown in 

figure 10.

Total PCB (sum of congeners 1016, 1221, 1232, 

1242, 1248, 1254, and 1260 or as total PCB’s). Polychlorinated biphenyls are complex mixtures containing 1 

to 8 chlorine atoms in 210 possible structural configurations (congeners). PCB’s are constituents of various 

industrial products such as hydraulic fluids and electrical transformers. Other past uses consisted of diverse 

applications such as in carbonless-copy papers, plasticizers, epoxy compounds, synthetic resins, machine 

and high-vacuum oils, compressor oils, textile dyes, 

putties, waxes, and pesticides (International Joint 

Commission, 1993). In 1979, manufacture and import 

of PCB’s were prohibited in the United States (International Joint Commission, 1993). PCB’s remaining in 

use are almost exclusively found in closed systems. 

Spills and leaks, however, result in releases to the 

environment. Of the 683 bed-sediment samples analyzed for PCB’s, 223 samples (32.7 percent) contained 

detectable PCB concentrations. Of the 223 samples 

with PCB detections, 67 sample concentrations ranged 

from the TEL to less than the PEL, 91 sample concentrations were from 1 to less than 10 times the PEL, 35 

sample concentrations were from 10 to less than 100 

times the PEL, and 27 sample concentrations were 

greater than 100 times the PEL (figs. 11 and B8, table 

3). Of the 460 samples with no PCB detections, detection limits for 100 and 360 samples were less than the 

TEL and PEL, respectively; thus, these samples were 

used for assessment purposes. 

The highest concentrations of PCB’s in bed sediment were found at the mouth of the River Raisin 

near Monroe, Michigan, in 1991 and 1993 (fig. 11). At 

this location, concentrations ranged from 53 to 40,000 

mg/kg. These concentrations were 191 to 145,000 

times the PEL. Other locations with PCB concentrations at least 10 times the PEL (listed in order of 

decreasing concentration) were in the Detroit River, 

Michigan; the main stem of the River Rouge, Michigan; the lower Clinton River, Michigan; Lake Saint 

Clair, Michigan; the Ottawa River at Toledo, Ohio; 

and a tributary to the Auglaize River, Ohio.

Polycyclic Aromatic Hydrocarbons

Polycyclic aromatic hydrocarbons (PAH’s) are considered to be the most acutely toxic component of petroleum products, and they are also associated with 

chronic and carcinogenic effects (Irwin and others, 

1997). Acute toxicity is rarely reported in humans, 

fish, or wildlife, as a result of exposure to low concentrations of a single PAH compound. PAH’s in general 

are more frequently associated with long-term chronic 

toxicity (Irwin and others, 1997). Exposure to PAH’s 

in bed sediment has resulted in liver and skin tumors 

in fish such as brown bullheads and white suckers and 

disruption of cellular or subcellular processes within 

organs or tissue of other organisms (Baumann and others, 1982; International Joint Commission, 1993; 

Smith and others, 1994)

Total PAH (sum of acenaphthene, acenaphthylene, anthracene, benzo[a]anthracene, 

benzo[a]pyrene, benzo[b]fluoranthene, 

benzo[ghi]perylene, benzo[k]fluoranthene, chrysene, 

dibenz[a,h]anthracene, fluoranthene, fluorene, 

indeno[1,2,3-cd]pyrene, naphthalene, phenanthrene, 

pyrene). PAH’s result from the incomplete combustion 

of organic carbon such as wood, municipal solid 

waste, tobacco, and fossil fuels such as coal, gasoline, 

and fuel oil. However, even natural occurrences such 

as forest fires introduce some PAH’s into bed sediments (National Research Council, 1983). 

Of the 414 bed-sediment samples analyzed for 

total PAH’s, 231 samples (55.8 percent) contained 

detectable concentrations. Of the 231 samples with 

total PAH detections, 77 sample concentrations ranged 

from the TEL to less than the PEL, 84 sample concentrations were from 1 to less than 10 times the PEL, 30 

sample concentrations ranged from 10 to less than 100 

times the PEL, and 4 sample concentrations were 

greater than 100 times the PEL (figs. 12 and B9, 

table 3). Of the 183 samples with no detections of total 

PAH’s, detection limits in 53 and 151 samples were 

less than the TEL and the PEL, respectively; thus, 

these samples were used for assessment purposes.

The highest concentrations of total PAH’s in bed 

sediment were found in a tributary to the Ottawa River 

at Toledo, Ohio in 1993, and the upper Clinton River, 

Michigan, in 1995 (fig. 12). At these locations, 

detected concentrations ranged from 470 to 2,657 mg/

kg. These concentrations were 138 to 781 times the 

PEL. Other sampling locations with concentrations 

greater than 10 times the PEL (listed in order of 

decreasing concentration) were the mouth of the River
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 19

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK

ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

MIREX CONCENTRATIONS

Not detected; detection limit equal to

or greater than LEL

Less than LEL

Aquatic effects (Persaud and others, 1993)

LEL - Lowest Effect Level (0.007 mg/kg)

SEL - Severe Effect Level (1.30 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK

ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

TOTAL PCB CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.0341 mg/kg)

PEL - Probable Effect Level (0.277 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 10. Total mirex concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 11. Total PCB concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
20 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Rouge, the Detroit River, and the main stem of the 

Clinton River, in Michigan; and the upper Cuyahoga 

River near Akron, the lower Cuyahoga River near 

Cleveland; and at the mouth of the Maumee River in 

Toledo, in Ohio.

Anthracene. Anthracene is a low-molecularweight, 3-ring PAH. Anthracene is used in industry as 

a source of dyestuffs and in coating applications 

(Parker, 1984). 

Of the 392 bed-sediment samples analyzed for 

anthracene, 76 samples (19.4 percent) contained 

detectable concentrations. Of the 76 samples with 

anthracene detections, 26 sample concentrations were 

ranged from the TEL to less than the PEL, 30 sample 

concentrations were from 1 to less than 10 times the 

PEL, 13 sample concentrations were from 10 to less 

than 100 times the PEL, and 3 sample concentrations 

were greater than 100 times the PEL (figs. 13 and B10, 

table 3). Of the 316 samples with no detections of 

anthracene, detection limits in 27 and 40 samples were 

less than the TEL and PEL, respectively; thus, these 

samples were used for assessment purposes. Lower 

detection limits could have made the data more useful.

The highest concentrations of anthracene in bed 

sediments were found in a tributary to the Ottawa 

River at Toledo, Ohio, in 1993; the Detroit River, 

Michigan, in 1996; and the lower River Rouge, Michigan, in 1993 (fig. 13). At these locations, anthracene 

concentrations ranged from 25 to 51 mg/kg, or 147 to 

300 times the PEL. Other locations where concentrations of anthracene exceeded the PEL (listed in order 

of decreasing concentration) were the main stem of the 

Clinton River, Michigan; the mouth of the Ashtabula 

River, Ohio; a tributary to the upper Cuyahoga River, 

Ohio; two tributaries to the lower Cuyahoga River, at 

Cleveland, Ohio; Lake Saint Clair, Michigan; and the 

upper and lower Maumee River, Indiana and Ohio. 

Benz[a]anthracene. Benz[a]anthracene is a 

high-molecular-weight, 4-ring PAH (Parker, 1984). 

Because it is formed when gasoline, garbage, or any 

animal or plant materials are burned, it is usually 

found in smoke and soot. Benz[a]anthracene is also 

found in creosote (Irwin and others, 1997). The 

sources of benz[a]anthracene are mainly urban and 

industrial.

Of the 393 bed-sediment samples analyzed for 

benz[a]anthracene, 158 samples (40.2 percent) contained detectable concentrations. Of the 158 samples 

with benz[a]anthracene detections, 65 sample concentrations ranged from the TEL to less than the PEL, 55 

sample concentrations were from 1 to less than 10 

times the PEL, 20 sample concentrations ranged from 

10 to less than 100 times the PEL, and 1 sample concentration was greater than 100 times the PEL (figs. 14 

and B11, table 3). Of the 235 samples with no detections of benz[a]anthracene, detection limits in 33 and 

84 samples were less than the TEL and PEL, respectively; thus, these samples were used for assessment 

purposes. Lower detection limits could have made the 

data more useful.

The highest concentration of benz[a]anthracene 

in bed sediment was found in a tributary to the Ottawa 

River at Toledo, Ohio, in 1993 (fig. 14). At this location, the benz[a]anthracene concentration was 160 mg/

kg or 416 times the PEL. Other locations where concentrations of benz[a]anthracene exceeded the PEL 

(listed in order of decreasing concentration) were the 

headwaters and main stem of the Clinton River, Michigan; the mouth of the River Rouge, Michigan; the 

Detroit River, Michigan; the Ottawa River at Toledo, 

Ohio; a tributary to and the lower main stem of the 

Cuyahoga River, at Cleveland, Ohio; a tributary to and 

the main stem of the Little Cuyahoga River at Akron, 

Ohio; the upper and lower main stem of the Maumee 

River, Ohio; the mouth of the Ashtabula River, Ohio; 

the middle main stem of the Cuyahoga River at Akron, 

Ohio; the mouth of the River Raisin, Michigan; Lake 

Saint Clair, Michigan; and the mouth of the Chagrin 

River, Ohio.

Benzo[a]pyrene. Benzo[a]pyrene is a highmolecular-weight, 5-ring PAH. The release of 

benzo[a]pyrene to the environment is widespread 

because it is a ubiquitous product of incomplete combustion (Irwin and others, 1997). Its sources are 

mainly industrial; coal-tar processing, petroleum refining, shale refining, coal and coke processing, kerosene 

processing, heat and power generation, combustion of 

tobacco, and combustion of fuels. Benzo[a]pyrene is 

found in runoff containing greases and oils, and it is a 

potential roadbed and asphalt leachate (Verschueren, 

1977). 

Of the 388 bed-sediment samples analyzed for 

benzo[a]pyrene, 147 samples (37.9 percent) contained 

detectable concentrations. Of the 147 samples with 

benzo[a]pyrene detections, 63 sample concentrations 

ranged from the TEL to less than the PEL, 59 sample 

concentrations were from 1 to less than 10 times the 

PEL, 9 sample concentrations were from 10 to less 

than 100 times the PEL, and 1 sample concentration 

was greater than 100 times the PEL (figs. 15 and B12,
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 21

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

TOTAL PAH CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Ingersoll and others, 1996)

TEL - Threshold Effect Level (0.26 mg/kg)

PEL - Probable Effect Level (3.4 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

LAKE ERIE UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

EXPLANATION

ANTHRACENE CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Ingersoll and others, 1996)

TEL - Threshold Effect Level (0.01 mg/kg)

PEL - Probable Effect Level (0.17 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Figure 12. Total PAH concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 13. Anthracene concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
22 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

table 3). Of the 241 samples with no detections of 

benzo[a]pyrene, detection limits for 31 and 241 samples were less than the TEL and PEL, respectively; 

thus, these samples were used for assessment purposes.

The highest concentrations of benzo[a]pyrene in 

bed sediment were found in tributaries to the Ottawa 

River near Toledo, Ohio, in 1992 and 1993; the entire 

main stem of the Clinton River, Michigan, in 1994 and 

1995; the mouth of the River Rouge, Michigan, in 

1993; and the Detroit River, Michigan, in 1996 (fig. 

15). At these locations, detected concentrations ranged 

from 9.3 to 110 mg/kg or 11.9 to 141 times the PEL. 

Other locations where concentrations of 

benzo[a]pyrene exceeded the PEL (listed in order of 

decreasing concentration) were the Cuyahoga River 

main stem and lower tributaries, Ohio; the Little Cuyahoga River, near Akron, Ohio; the mouth of the Ashtabula River, Ohio; the lower Maumee River, Ohio; 

the mouth of the River Raisin, Michigan; and Lake 

Saint Clair, Michigan.

Chrysene. Chrysene, a 4-ring PAH, is a component in coal tar and is present in exhaust from gasoline 

engines (Verschueren, 1977). Chrysene is usually 

found in smoke and soot, coal tar, coke oven emissions, and cigarette smoke (U.S. Environmental Protection Agency, 1997b). 

Of the 396 bed-sediment samples analyzed for 

chrysene, 189 samples (47.7 percent) showed detectable concentrations. Of the 189 samples with chrysene 

detections, 86 sample concentrations ranged from the 

TEL to less than the PEL, 65 sample concentrations 

were from 1 to less than 10 times the PEL, 11 sample 

concentrations were from 10 to less than 100 times the 

PEL, and 1 sample concentration was greater than 100 

times the PEL (figs.16 and B13, table 3). Of the 207 

samples with no detections of chrysene, detection limits for 35 and 179 samples were less than the TEL and 

PEL, respectively; thus, these samples were used for 

assessment purposes. 

The highest concentrations of chrysene in bed 

sediment were found in tributaries to the Ottawa River, 

near Toledo, Ohio, in 1992 and 1993; the main stem of 

the Clinton River, Michigan, in 1994 and 1995; the 

mouth of the River Rouge, Michigan, in 1993; and the 

Detroit River, Michigan, in 1996 (fig. 16). At these 

locations, detected concentrations ranged from 8.7 to 

180 mg/kg. These concentrations were 10.1 to 209 

times the PEL. Other locations where concentrations 

of chrysene in bed sediment exceeded the PEL (listed 

in order of decreasing concentration) were the tributaries to and the lower main stem of the Cuyahoga River, 

Ohio; the lower Maumee River, Ohio; the mouth of the 

Ashtabula River, Ohio; the Little Cuyahoga River, 

near Akron, Ohio; the mouth of the River Raisin, 

Michigan; Lake Saint Clair, Michigan; and the mouth 

of the Chagrin River, Ohio.

Phenanthrene. Phenanthrene, a low-molecularweight 3-ring PAH. It is naturally present in coal and 

petroleum and is used in industry and in the synthesis 

of dyes and drugs (Parker, 1984). Phenanthrene is a 

high-temperature combustion product of coal and 

petroleum (U.S. Environmental Protection Agency, 

1993d). 

Of the 398 bed-sediment samples analyzed for 

phenanthrene, 187 samples (47.0 percent) showed 

detectable concentrations. Of the 187 samples with 

phenanthrene detections, 66 sample concentrations 

ranged from the TEL to less than the PEL, 74 sample 

concentrations were from 1 to less than 10 times the 

PEL, 19 sample concentrations were from 10 to less 

than 100 times the PEL, and 2 sample concentrations 

were more than 100 times the PEL (figs. 17 and B14, 

table 3). Of the 211 samples with no detections of 

phenanthrene, detection limits for 30 and 112 samples 

were less than the TEL and PEL, respectively; thus, 

these samples were used for assessment purposes. 

Lower detection limits could have made the data more 

useful. 

The highest concentrations of phenanthrene in 

bed sediment were found in tributaries to the Ottawa 

River near Toledo, Ohio, in 1992 and 1993; the lower 

River Rouge, Michigan, in 1993; along the main stem 

of the Clinton River, Michigan, in 1994 and 1995; the 

Detroit River, Michigan, in 1996; and the mouth of the 

Ashtabula River, Ohio, in 1996 (fig. 17). At these 

locations, detected concentrations ranged from 5.2 to 

600 mg/kg. These concentrations were 10.1 to 1,165 

times the PEL. Other locations where concentrations 

of phenanthrene in bed sediment exceeded the PEL 

(listed in order of decreasing concentration) were the 

tributaries to and the lower main stem of the Cuyahoga 

River, Ohio; the Little Cuyahoga River, near Akron, 

Ohio; the mouth of Rocky River, Ohio; the lower 

Maumee River, Ohio; Lake Saint Clair, Michigan; the 

lower Chagrin River, Ohio; the upper Maumee River, 

Indiana; the mouth of the Black River, Ohio; the 

Ottawa River at Lima, Ohio; and the mouth of the 

River Raisin, Michigan.
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 23

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

BENZ[a]ANTHRACENE CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.0317 mg/kg)

PEL - Probable Effect Level (0.385 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

BENZO[a]PYRENE CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.0319 mg/kg)

PEL - Probable Effect Level (0.782 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 14. Benz[a]anthracene concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair 

Drainages, 1990–97.

Figure 15. Benzo[a]pyrene concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
24 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

CHRYSENE CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.0571 mg/kg)

PEL - Probable Effect Level (0.862 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

PHENANTHRENE CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Equal to or greater than 100 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.0419 mg/kg)

PEL - Probable Effect Level (0.515 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 16. Chrysene concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 17. Phenathrene concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 25

Trace Metals

Trace metals in bed sediment are derived from a variety of sources including weathering of rocks and soils 

and input from anthropogenic sources. Trace metals at 

naturally occurring concentrations generally are not 

harmful to aquatic life; however, the high end of the 

natural concentration range typically falls in the lower 

range of the various sediment-quality criteria, an overlap that can seriously confound interpretation. Of all 

the contaminants discussed in this report, trace metals 

were those detected most frequently in streambed and 

lakebed sediments. Elevated concentrations in bed 

sediment are of particular interest because some trace 

metals may be toxic to and accumulate in aquatic 

organisms. Avenues by which trace metals are introduced into bed sediments include atmospheric deposition, industrial emissions (especially from activities 

such as plating, smelting, and refining), wastewater 

discharges, landfills, stormwater runoff, and automobile exhaust. The extensive use of trace metals in 

industry often results in concentrations far greater than 

natural levels (Armitage, 1995). Certain trace metals 

are known to be highly toxic and bioaccumulative in 

food chains, but little is known about the occurrence 

and biological significance of others.

Arsenic (semi-metallic element). Sources of 

arsenic include wood preservatives, herbicides, and 

insecticides; however, arsenic compounds are present 

naturally in some waters. Lead arsenate and calcium 

arsenate have been applied extensively as miticides 

and pesticides on orchard crops. Additional uses 

include metal-ore processing, glassware, ceramics, 

leather tanning, chemical industries, pigmentation in 

paints, and additives in medical treatments (Michigan 

Water Resources Commission, 1972). 

Of the 480 bed-sediment samples analyzed, 

arsenic was detected in 470 samples (97.9 percent). Of 

the 470 samples with arsenic detections, 269 sample 

concentrations ranged from the TEL to less than the 

PEL, 58 sample concentrations were from 1 to less 

than 10 times the PEL, and 2 sample concentrations 

were from 10 to less than 100 times the PEL (figs.18 

and B15, table 3). Of the 10 samples with no detections of arsenic, detection limits in 1 and 10 samples 

were less than the TEL and the PEL, respectively; 

thus, all samples were used for assessment purposes. 

The highest concentrations of arsenic in bed 

sediment were found in a small tributary to Lake Erie, 

near North Kingsville, Ohio, in 1993 and 1995; a tributary to the main stem of the Cuyahoga River, Ohio, in 

1991; the lower Rocky River, Ohio, in 1992; and the 

mouth of the River Raisin, Michigan, in 1993 (fig. 18). 

At these locations, detected concentrations ranged 

from 33 to 649 mg/kg. These concentrations were 

from 1.9 to 38.2 times the PEL. Other locations with 

elevated concentrations of arsenic greater than the 

PEL (listed in order of decreasing concentration) were 

the Blanchard River near Findlay, Ohio; Ottawa River 

at Toledo, Ohio; a tributary to the main stem of the 

Auglaize River, Ohio; Ottawa River near Lima, Ohio; 

the upper Clinton River, Michigan; Cuyahoga River 

near Akron, Ohio; the mouth of the Ashtabula River, 

Ohio; the upper Huron River, Michigan; the upper 

River Raisin, Michigan; the mouth of the Cuyahoga 

River, Ohio; the Detroit River, Michigan; and the 

upper St. Marys River, Ohio.

Cadmium. Industrial use of cadmium has been in 

metallurgy to alloy with copper, lead, silver, aluminum, and nickel. Cadmium also is used in electroplating, ceramics, pigmentation, photography, and nuclear 

reactors. Cadmium salts are sometimes employed as 

insecticides and antihelminthics (Michigan Water 

Resources Commission, 1972). Other sources of cadmium emissions are releases to the environment from 

fossil-fuel use, fertilizer applications, and sewagesludge disposal (Shelton, 1990). Trace amounts of 

cadmium occur naturally, chiefly as a sulfide salt. Cadmium is found in very low concentrations in most 

rocks, in coal and petroleum, and often in combination 

with zinc.

Of the 616 bed-sediment samples analyzed for 

cadmium, 588 samples (95.5 percent) showed detectable concentrations. Of the 588 samples with cadmium 

detections, 198 sample concentrations ranged from the 

TEL to less than the PEL, and 114 sample concentrations were from 1 to less than 10 times the PEL 

(figs.19 and B16, table 3). Of the 28 samples with no 

detections of cadmium, detection limits for 1 and 27 

samples were less than the TEL and the PEL, respectively; thus, all samples were used for assessment purposes. 

The highest concentrations of cadmium in bed 

sediment were found in the main stem of the Clinton 

River, Michigan, in 1994 and 1995; the mouth of the 

Cuyahoga River, Ohio, in 1993; the Detroit River, 

Michigan, in 1996; the main stem of the Black River, 

Ohio, in 1992; and the main stem of the River Rouge, 

Michigan, in 1993 (fig. 19). At these locations, 

detected cadmium concentrations ranged from 10.0 to 

28 mg/kg. These concentrations were 2.8 to 7.9 times
26 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE ERIE

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

ARSENIC CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (5.9 mg/kg)

PEL - Probable Effect Level (17 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

CADMIUM CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.596 mg/kg)

PEL - Probable Effect Level (3.53 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 18. Arsenic concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 19. Cadmium concentrations in streambed and lakebed sediments, Lake Erie–Lake S Clair Drainages, 

1990–97.
Areal Distribution and Concentrations of Contaminants of Concern in Surficial Bed Sediments 27

the PEL. Other locations where concentrations of cadmium in bed sediments exceeded the PEL (listed in 

order of decreasing concentration) were the upper 

Cuyahoga River near Akron, Ohio; Ottawa River at 

Toledo, Ohio; upper Blanchard River near Findlay, 

Ohio; the mouth of the River Raisin, Michigan; Lake 

Saint Clair, Michigan; Ottawa River near Lima, Ohio; 

and the lower Maumee River, Ohio.

Copper. Metallic copper is used extensively in 

the electrical industry, in many alloys for cooking utensils, and for water pipes and roofing. Copper salts are 

used in textile processes, pigmentation, tanning, photography, engraving, electroplating, insecticides, fungicides, control of algae and other aquatic growths, and 

many other industrial processes. Copper is a known 

contaminant in urban stormwater runoff (Michigan 

Water Resources Commission, 1972). 

Of the 587 bed-sediment samples analyzed for 

copper, 586 samples (99.8 percent) showed detectable 

concentrations. Of the 586 samples with copper detections, 209 sample concentrations ranged from the TEL 

to less than the PEL, and 14 sample concentrations 

were from 1 to less than 10 times the PEL (figs. 20 and 

B17, table 3). All samples were used for assessment 

purposes.

The highest concentrations of copper in bed sediment were found in the main stem and East Branch of 

the Portage River, Ohio, in 1994; the Ottawa River 

near Toledo, Ohio, in 1996; the Detroit River, Michigan, in 1996; the mouth of the Cuyahoga River, Ohio, 

in 1996; the mouth of Black River, Ohio, in 1996; the 

mouth of the River Raisin, Michigan, in 1992; and the 

River Rouge, Michigan, in 1993 (fig. 20). At these 

locations, detected concentrations ranged from 200 to 

649 mg/kg and were 1 to 3.2 times the PEL.

Lead. In the past, a major use of lead was the 

antiknock agent tetraethyl lead in gasoline. Other uses 

include leaded glass, storage batteries, plumbing, and 

lead oxides and pigments in paint. Lead is released as a 

waste byproduct from coal and oil combustion, metal 

refining and fabrication, cement manufacture, and 

waste incineration. Lead is a known contaminant in 

urban stormwater runoff and in landfill leachate (Michigan Water Resources Commission, 1972). 

Of the 615 bed-sediment samples analyzed for 

lead, 614 samples (99.8 percent) showed detectable 

concentrations. Of the 614 samples with detectable 

lead, 156 sample concentrations ranged from the TEL 

to less than the PEL, and 109 sample concentrations 

were from 1 to less than 10 times the PEL (figs. 21 and 

B18, table 3). All samples were used for assessment 

purposes.

The highest concentrations of lead in bed sediment were found in a tributary to and the mainstem of 

the Ottawa River near Toledo, Ohio, in 1992; the 

mouth of the River Rouge, Michigan, in 1993; the 

lower Cuyahoga River near Cleveland, Ohio, in 1990; 

the mouth and the main stem of the Clinton River, 

Michigan, in 1995; the Detroit River, Michigan, in 

1996; and the Ottawa River near Lima, Ohio, in 1991 

(fig. 21). At these locations, lead concentrations ranged 

from 260 to 589 mg/kg and were 2.8 to 6.4 times 

greater than the PEL. Other locations where concentrations of lead in bed sediments exceeded the PEL (listed 

in order of decreasing concentration) were the mouth 

of the River Raisin, Michigan; Lake Saint Clair, Michigan; the lower Maumee River, Ohio; the upper Cuyahoga River, near Akron, Ohio; the headwaters of the 

Clinton River, Michigan; the main stem of the Chagrin 

River, Ohio; and the Little Cuyahoga River near 

Akron, Ohio.

Mercury. Mercury is a volatile metal that can 

exist in metallic, elemental, inorganic salt, and organic 

compound forms. Methyl mercury is an example of the 

latter. These various forms have different properties 

and toxicities. Mercury is widely used within the 

industrial, medical, agricultural, and consumer sectors; 

more than 2,000 applications have been identified. 

Coal combustion and municipal and medical waste 

incineration are the major anthropogenic sources to the 

atmosphere (Irwin and others, 1997). Most biocidal 

and fungicidal uses and use in paints have now been 

canceled. Mercury is released as a waste byproduct in 

metal smelting and battery manufacturing, waste incineration, and disposal of batteries and other consumer 

goods. Implementation of pollution controls and closures of chlorine and caustic soda manufacturing plants 

have reduced releases of mercury to the environment 

(International Joint Commission, 1993). Global atmospheric transport of mercury through rainfall is a common source. 

Of the 465 bed-sediment samples analyzed for 

mercury, 309 samples (66.4 percent) showed detectable concentrations. Of the 309 mercury detections, 59 

sample concentrations ranged from the TEL to less 

than the PEL, 51 sample concentrations were from 1 to 

less than 10 times the PEL, and 4 sample concentrations were from 10 to less than 100 times the PEL 

(figs. 22 and B19, table 3). Of the 156 samples with no
28 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

LEAD CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (35 mg/kg)

PEL - Probable Effect Level (91.3 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

COPPER CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (35.7 mg/kg)

PEL - Probable Effect Level (197 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Cleveland Toledo

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

LEAD CONCENTRATIONS

Not detected; detection limit equal to

 or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (35 mg/kg)

PEL - Probable Effect Level (91.3 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 21. Lead concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 20. Copper concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
Sediment Contamination and Potential Impairments of Aquatic Life 29

detections of mercury, detection limits in 152and 155 

samples were less than the TEL and the PEL, respectively. All samples were used for assessment purposes.

The highest concentrations of mercury in bed 

sediment were found in 1996 in the Detroit River, 

Michigan, and the Little Cuyahoga River near Akron, 

Ohio (fig. 22). At these locations, detected concentrations ranged from 6.06 to 16.0 mg/kg and were 12.5 to 

32.8 times the PEL. Other locations where concentrations of mercury in bed sediments exceeded the PEL 

(listed in order of decreasing concentration) were the 

mouth of River Raisin, Michigan; Lake Saint Clair, 

Michigan; the Monroe Harbor, in Lake Erie; the mouth 

of the River Rouge, Michigan; and the mouth of the 

Clinton River, Michigan.

Zinc. Elemental zinc has been used extensively 

for galvanizing, alloys, electrical purposes, printing 

plates, dye manufacture, dyeing processes, and many 

other industrial processes. Zinc is a known contaminant in urban stormwater runoff and in landfill 

leachate, and it is leachable from galvanized pipes 

used as culverts. Zinc salts are used in paint pigments, 

cosmetics, pharmaceuticals, dyes, and pesticides and 

fertilizers. Industrial wastes sometimes contain high 

concentrations of zinc (Michigan Water Resources 

Commission, 1972). 

Of the 575 bed-sediment samples analyzed for 

zinc, 100 percent showed detectable concentrations. 

167 sample concentrations ranged from the TEL to 

less than the PEL, and 82 sample concentrations were 

from 1 to less than 10 times the PEL (figs. 23 and B20, 

table 3). The highest concentrations of zinc in bed sediments were found in the Detroit River, Michigan, in 

1996; the mouth of the Maumee River, Ohio, in 1996; 

the mouth of the River Rouge, Michigan, in 1993; the 

mouth of the Cuyahoga River, Ohio, in 1996; and the 

mouth of the Clinton River, Michigan, in 1995 (fig. 

23). At these locations, detected concentrations ranged 

from 830 to 2,300 mg/kg. These concentrations were 

2.6 to 7.3 times the PEL. 

Other locations where concentrations of zinc in 

bed sediments exceeded the PEL (listed in order of 

decreasing concentration) were the mouth of the Black 

River, Ohio; the headwaters of the Portage River, 

Ohio; the main stem of the Ottawa River, at Toledo, 

Ohio; the lower River Raisin, Michigan; the main stem 

of the Clinton River, Michigan; the Ottawa River near 

Lima, Ohio; the mouth of the Rocky River, Ohio; the 

Little Cuyahoga River at Akron, Ohio; and the mouth 

of the Ashtabula River, Ohio.

Sediment Contamination and Potential Impairments of Aquatic Life

The extent to which contaminant concentrations are in 

excess of sediment-quality guidelines indicates the 

potential for impairment of aquatic life (table 4, fig. 

24). The link between the organisms most at risk for 

impairment and exposure to surficial sediments is 

strong because benthic macroinvertebrates and fish 

live in or forage near the surface of these sediments. 

Information presented in this section compares sediment contamination in AOC’s to sediment contamination outside of AOC’s. AOC’s represent some of the 

most highly contaminated bed-sediment areas in the 

Lake Erie–Lake Saint Clair Drainages. Additional 

analysis ranked areas where multiple contaminants 

exceed PEL’s and SEL’s to show the most severe sediment contamination.

Occurrence and Magnitude of Potential Impairments

Trace-elements were the most frequently detected contaminants of the 20 contaminants investigated for this 

report; yet the potential for impairment of aquatic 

organisms in the Lake Erie–Lake Saint Clair Drainages was most often indicated by the concentrations of 

PAH’s, DDT, and PCB’s (table 4; fig. 24). Zinc was 

detected in 100 percent of surficial bed-sediment samples, and lead, copper, arsenic, and cadmium were 

detected in more than 95 percent of the samples. Of 

the trace-metals group, mercury was detected at the 

lowest frequency, in 67 percent of the samples. Of the 

six trace metals, cadmium and lead were the most 

likely to exceed a PEL, whereas copper was the least 

likely to exceed a PEL (Smith and others, 1996). 

Compared to trace metals, the next most frequently detected group of contaminants in aquatic sediments were the PAH’s. Concentrations of total PAH, 

chrysene, phenanthrene, benz[a]anthracene, and 

benzo[a]pyrene were detected in 37.9 to 55.8 percent 

of surficial bed-sediment samples. Anthracene concentrations were the exception, being detected in only 

19.4 percent of samples. Concentrations of total DDT 

and total PCB were detected in surficial bed sediments 

at similar frequencies (35.4 percent for total DDT and 

37.6 percent for PCB’s). The remaining organochlorine compounds of concern (total chlordane, dieldrin 

plus aldrin, hexachlorobenzene, total hexachlorocyclohexane, lindane, and total mirex) were detected at 

much lower frequencies than trace metals, PAH’s, total 

PCB’s, and total DDT. The percentage of sample val-
30 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

MERCURY CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Equal to or greater than 10 times PEL

and less than 100 times the PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (0.174 mg/kg)

PEL - Probable Effect Level (0.486 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Cleveland Toledo

Akron

Fort 

Wayne

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

CANADA

NEW YORK ONTARIO

MICHIGAN

ONTARIO

UNITED STATES

LAKE

HURON

LAKE ONTARIO

LAKE

ST. CLAIR

EXPLANATION

ZINC CONCENTRATIONS

Not detected; detection limit equal to

or greater than TEL

Less than TEL

Equal to or greater than TEL and

less than PEL

Equal to or greater than PEL and

less than 10 times PEL

Aquatic effects (Smith and others, 1996)

TEL - Threshold Effect Level (123 mg/kg)

PEL - Probable Effect Level (315 mg/kg)

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

LAKE ERIE

Buffalo

Detroit

Erie

Toledo Cleveland

Akron

Fort 

Wayne

Figure 22. Mercury concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 

1990–97.

Figure 23. Zinc concentrations in streambed and lakebed sediments, Lake Erie–Lake Saint Clair Drainages, 1990–97.
Sediment Contamination and Potential Impairments of Aquatic Life 31

ues exceeding a PEL (Smith and others, 1996; Ingersoll and others, 1996) was greater for individual PAH’s 

than for trace metals or total PCB’s. The percentage of 

sample values exceeding a SEL (Persaud and others, 

1993) was greater for total DDT, copper, total PCB’s, 

and total PAH’s than for any other contaminants of 

concern listed in this report. The number of observations, frequency of detection, and the percentage probability of sample concentrations to exceed a sedimentquality guideline are listed in table 4. 

Contamination within and outside of Areas of Concern

In 1987, the International Joint Commission (IJC) 

identified 12 Areas of Concern (AOC’s) in the Lake 

Erie–Lake Saint Clair Drainages (fig. 25) where 

aquatic health has been harmed. These geographic 

areas are mostly represented by river mouths, harbors, 

and connecting channels. In some cases, an entire sub 

basin is designated as an AOC. In most cases, the primary reason AOC’s were designated was the documented contamination of sediments and its potential 

impact on aquatic health and habitat. 

AOC’s within the Lake Erie–Lake Saint Clair 

Drainages typically comprise river segments in the 

most heavily industrialized centers. They include the 

following: 

Michigan—Clinton River, River Rouge, the 

mouth of the River Raisin at Monroe Harbor, and the 

Detroit River and Saint Clair River connecting channels including their tributaries; 

Ohio—The downstream segments of the 

Maumee River and Ottawa River and their adjacent 

Lake Erie shoreline tributaries, the Black River, the 

lower Cuyahoga River and adjacent Lake Erie shoreline, and the mouth of the Ashtabula River; 

Pennsylvania—Presque Isle Bay; 

New York—the mouth of the Buffalo River and 

the Niagara River connecting channel. These last two 

AOC’s were not evaluated because data were not 

available in digital form.

The star diagrams (figs. 26 and 27), referred to 

in the following sections of the report, represent the 

75th- and 90th-percentile concentrations of selected 

trace metals and organic compounds in relation to sediment-quality guidelines within and outside of AOC’s 

in the United States. The 75th- and 90th-percentile 

concentrations are the concentrations that are 

exceeded in 25 and 10 percent of all samples, respectively. For all contaminants shown in figures 26 and 

27, concentrations associated with the 75th and 90th 

percentiles were measured values because detection 

frequencies for those contaminants were greater than 

25 percent.

Trace metals. Except for arsenic, selected trace metals 

were detected somewhat more frequently and at 

slightly greater concentrations within AOC’s than outside AOC’s (fig. 26). Within AOC’s, detection frequencies for copper, lead, and zinc were 100 percent 

and were greater than those for arsenic (78 percent), 

cadmium (97 percent), and mercury (69 percent). Outside AOC’s, detection frequencies for copper, lead, 

and zinc were 100 percent and were greater than those 

for arsenic (96 percent), cadmium (94 percent), and 

mercury (63 percent). Within AOC’s, the top 25 percent of selected trace-metal concentrations were 

greater than their corresponding TEL’s. Outside 

AOC’s, the top 25 percent of trace-metal concentrations, except for mercury, were greater than their 

TEL’s. Within AOC’s, the top 10 percent of tracemetal concentrations, except for copper, were greater 

than their respective PEL’s (fig. 26). Outside AOC’s, 

the top 10 percent of selected trace-metal concentrations, except for copper and mercury, were greater 

than their PEL’s. 

Organic compounds. Organic compounds were 

detected much more frequently and at much greater 

concentrations within AOC’s than outside AOC’s. In 

AOC’s, total PAH’s were detected at the greatest frequency (71 percent), followed by phenanthrene (62 

percent), benz[a]anthracene (52 percent), 

benzo[a]pyrene (51 percent), total DDT (42 percent), 

and total PCB (39 percent) (fig. 27). Outside AOC’s, 

total PAH’s were detected at the greatest frequency (39 

percent), followed by phenanthrene (31 percent), 

benz[a]anthracene (28 percent), benzo[a]pyrene (24 

percent), total DDT (29 percent), and total PCB (19 

percent) (fig. 27). In AOC’s, the top 25 percent of 

selected organic-compound concentrations were far 

greater than their TEL’s, and except for total DDT, 

were also somewhat greater than their PEL’s (fig. 27). 

Outside AOC’s, the top 25 percent of all selected 

organic-compound concentrations were somewhat 

greater than their TEL’s and except for total PCB and 

total DDT, were equal to or slightly greater than their 

PEL’s (fig. 27). Within AOC’s, the top 10 percent of 

selected organic-compound concentrations, except 

total DDT, were more than 10 times greater than their 

PEL’s. Outside AOCs, the top 10 percent of selected 
32 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

OHIO

MICHIGAN

INDIA

OHIO

NA

PENNSYLVANIA

NEW YORK

PENNSYLVANIA

OHIO

LAKE

HURON

LAKE ONTARIO

EXPLANATION

Lake Erie-Lake St. Clair Basin

Areas of Concern

Tributaries and coastlines within Areas

of Concern

86° 85° 83° 80° 79°

40°

42°

43°

44° 84° 82° 81° 78°

41°

20 40 60 MILES

0 20 40 60 KILOMETERS

0

St. Clair River

Clinton River

Rouge River

Detroit River

Weatley Harbor

Monroe Harbor

Maumee River and 

Nearshore Tributaries

Black River

Cuyahoga

River

Ashtabula River

Presque Isle Bay

Buffalo River

Niagara River

0

10

20

30

40

50

60

70

80

90

100

Zinc

Lead

Copper

 Arsenic

 Cadmium

Mercury

Total PAH

Chrysene

 Phenanthrene

 Benz (a) anthracene

 Benzo (a) pyrene

Total DDT

Total PCB

 Anthracene

 Dieldrin/aldrin

 Hexachlorocyclohexane

 Chlordane

 Lindane (γ-HCH)

 Hexachlorobenzene

 Mirex/photomirex

CONTAMINANT

FREQUENCY, IN PERCENT

Percentage of samples with detected

concentrations

Percentage of samples with concentrations

equal to or greater than a Probable Effect Level

Percentage of samples with concentrations

equal to or greater than a Severe Effect Level

Figure 25. Areas of Concern (in red) in the Lake Erie–Lake Saint Clair Drainages (International Joint Commission, 

1987).

Figure 24. Frequency of detection and percentage of sample concentrations exceeding a sedimentquality guideline; Lake Erie–Lake Saint Clair Drainages, 1990–97.
Sediment Contamination and Potential Impairments of Aquatic Life 33

Table 4. Probability of sample concentrations being equal to or greater than a sediment-quality guideline, Lake Erie–Lake 

Saint Clair Drainages, 1990–97 

[N, number of samples; LEL, Lowest Effect Level; SEL, Severe Effect Level; USEPA, U.S. Environmental ProtectionAgency; TEL,Threshold 

Effect Level; PEL, Probable Effect Level; --, no guideline; i.d., insufficient data to compute exceedance percentage (less than 25 percent of the 

samples had detected values); bold type, data used in figure 24; values represent detected concentrations or nondetected concentrations greater 

than guidelines]

Probability of sample concentrations being equal to or 

greater than a guideline (in percent)

Na

(percent of N 

with 

detected values)

a

 If detection rate was less than 25 percent of N, exceedance percentage was not computed.

Ontario–

Provincial Sediment Quality 

Guidelinesb

b Persaud and others, 1993.

USEPA–Great 

Lakes

Sediment Effect

Concentrationsc

c

 Ingersoll and others, 1996.

Environment 

Canada–

Great Lakes 

Guidelinesd

d Smith and others, 1996.

Contaminant LEL SEL TEL PEL TEL PEL

Organochlorine compounds

Chlordane, total 371 (7.82) i.d. i.d. -- -- i.d. i.d.

DDT, total 409 (35.4) 59.8 40.7 -- -- 59.8 0.20

Dieldrin plus aldrin 407 (11.0) i.d. i.d. -- -- i.d. i.d.

Hexachlorobenzene 411 (1.46) i.d. i.d. -- -- -- --

Hexachlorocyclohexane, total 407 (11.0) i.d. i.d. -- -- -- --

Lindane 404 (2.72) -- -- -- -- i.d. i.d.

Mirex, total 199 (0.00) i.d. i.d. -- -- -- --

PCB, total 683 (37.6) 66.0 7.8 87.2 25.4 84.8 23.8

Polycyclic aromatic hydrocarbon compounds

PAH, total 414 (55.8) 30.7 4.73 78.6 36.1 -- --

Anthracene 392 (19.4) i.d. i.d. i.d. i.d. -- --

Benz[a]anthracene 393 (40.2) 64.0 1.45 88.9 66.8 87.3 57.7

Benzo[a]pyrene 388 (37.9) 62.1 1.20 88.2 66.0 88.2 30.0

Chrysene 396 (47.7) 61.9 4.30 87.5 59.2 89.5 26.4

Phenanthrene 398 (47.0) 47.9 3.39 87.1 59.7 85.8 48.8

Trace metals

Arsenic 480 (97.9) 68.6 1.17 29.3 0.84 69.7 11.8

Cadmium 616 (95.4) 53.2 2.37 55.4 22.5 33.2 18.3

Copper 587 (99.8) 69.6 9.13 47.4 11.2 37.7 1.32

Lead 615 (99.8) 46.4 2.54 41.7 19.9 42.8 17.6

Mercury 465 (66.4) 23.7 1.33 -- -- 25.4 12.1

Zinc 575 (100) 44.4 1.89 53.8 5.12 43.3 14.1
34 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

organic-compound concentrations, except for DDT, 

were only equal to or slightly greater than their PEL’s.

Comparative Ranks by Location

Compared to the area as a whole, the highest detection 

frequencies and highest concentrations of total PCB’s 

and total PAH’s in the Lake Erie–Lake Saint Clair 

Drainages were in AOC’s. Because the AOC’s are in 

the largest urban areas (those with populations greater 

than 100,000), contamination is usually considered to 

be related to major cities and urban land use. The highest concentrations of anthracene, total PAH, phenanthrene, benz[a]anthracene, total PCB, chrysene, 

benzo[a]pyrene, and total chlordane in bed sediment 

were in AOC’s along the following large rivers: Clinton River, Detroit River, River Raisin, and River 

Rouge, in Michigan; and the Maumee River and Cuyahoga River in Ohio. Total DDT, total dieldrin, 

hexachlorocyclohexane, and lindane, at concentrations 

greater than their PEL’s or SEL’s, were reported in 

streams draining urban and agricultural areas throughout the Lake Erie–Lake Saint Clair Drainages, an indication that sources are present in both types of land 

use. Mirex and hexachlorobenzene were not found to 

any great extent in samples; however, lower detection 

limits for hexachlorobenzene would improve confidence in this assessment. 

The highest detection frequencies and concentrations of most trace metals were not dramatically 

greater in AOC’s than in other areas of the Drainages. 

Trace elements within AOC's Trace elements outside of AOC's

EXPLANATION

Concentrations in milligrams per kilogram

Compound (percent detected): n=sample population

 75th percentile

 90th percentile

Threshold Effect Level (TEL)

Probable Effect Level (PEL)

Arsenic (78%): n = 405

Cadmium (97%): n = 309

Copper (100%): n = 295

Mercury (69%): n = 259

Lead (100%): n = 307

Zinc (100%): n = 282

Arsenic (96%): n = 214

Cadmium (94%): n = 306

Copper (100 %): n = 290

Mercury (63%): n = 206

Lead (100%): n = 306

Zinc (100%): n = 291

Arsenic (78%): n = 405

Cadmium (97%): n = 309

Copper (100%): n = 295

Mercury (69%): n = 259

Lead (100%): n = 307

Zinc (100%): n = 282

Arsenic (96%): n = 214

Cadmium (94%): n = 306 

Copper (100 %): n = 290

Mercury (63%): n = 206

Lead (100%): n = 306

Zinc (100%): n = 291

 1000

 100

 10

 0.1

 1

 1000

 100

 10

 0.1

 1

 1000

 100

 10

 0.1

 1

 1000

 100

 10

 0.1

 1

Figure 26. Star diagrams showing 75th- and 90th-percentile concentrations of selected trace element contaminants 

in relation to sediment-quality guidelines within and outside of Areas of Concern, Lake Erie–Lake Saint Clair Drainages, 

1990–97.
Sediment Contamination and Potential Impairments of Aquatic Life 35

The dominant factor that may be influencing the concentrations of cadmium, copper, lead, and mercury in 

the bed sediment appears to be the presence of urban 

land in drainage areas of receiving streams. Tracemetal concentrations in many principal streams in 

Lake Erie–Lake Saint Clair Drainages were frequently 

greater than sediment-quality guidelines. Because the 

concentrations of some trace metals in soils vary naturally (depending on the type of surficial and bedrock 

materials from which they are derived), distinguishing 

the primary sources of arsenic and zinc may be complicated.

A ranking of the 10 most heavily contaminated 

rivers in the Lake Erie–Lake Saint Clair Drainages 

was based on the frequency of exceeding one or more 

PEL’s (table 5). The Ottawa River at Toledo, Ohio, 

ranked first, with six contaminants of concern detected 

at concentrations greater than 100 times their PEL’s; 

the Ashtabula River, in Ohio, ranked tenth, with the 

concentration of only one contaminant of concern 

greater than 10 times the PEL (table 5). Maximum 

concentrations of contaminants ranged from 4.9 times 

the PEL for total DDT at the mouth of the Clinton 

River, in Michigan, to 145,000 times the PEL for total 

PCB’s at the mouth of the River Raisin, in Michigan. 

In the Ottawa River Drainages at Toledo, Ohio, maximum concentrations of 15 contaminants were greater 

than their PEL’s. Maximum concentrations of 

anthracene, total PAH, phenanthrene, 

benz[a]anthracene, chrysene, and benzo[a]pyrene 

ranged from 141 to 1,165 times their respective PEL’s. 

Maximum concentrations of total PCB’s and dieldrin 

plus aldrin ranged from 10 to less than 100 times their 

PEL’s. Maximum concentrations of total chlordane, 

Trace organic compounds outside of AOC's

Benz[a]anthracene (28%): n = 195

Benzo[a]pyrene (24%): n = 193

Phenanthrene (31%): n = 195

Total DDT (29%): n = 208

Total PAH (39%): n = 192

Total PCB (19%): n = 208

Trace organic compounds within AOC's

Benz[a]anthracene (52%): n = 199

Benzo[a]pyrene (51%): n = 196

Phenanthrene (62%): n = 204

Total DDT (42%): n = 201

Total PAH (71%): n = 222

Total PCB (39%): n = 475

Benz[a]anthracene (52%): n = 199

Benzo[a]pyrene (51%): n = 196

Phenanthrene (62%): n = 204

Total DDT (42%): n = 201

Total PAH (71%): n = 222

Total PCB (39%): n = 475

Benz[a]anthracene (28%): n = 196

Benzo[a]pyrene (24%): n = 193

Phenanthrene (31%): n = 195

Total DDT (29%): n = 208

Total PAH (39%): n = 192

Total PCB (19%): n = 208

EXPLANATION

Concentrations in milligrams per kilogram

Compound (percent detected): n=sample population

 75th percentile

 90th percentile

Threshold Effect Level (TEL)

Probable Effect Level (PEL)

 100

 10

 1

 0.01

 0.1

 0.001

 100

 10

 1

 0.01

 0.1

 0.001

 100

 10

 1

 0.01

 0.1

 0.001

 100

 10

 1

 0.01

 0.1

 0.001

Figure 27. Star diagrams showing 75th- and 90th-percentile concentrations of selected organic compound contaminants in 

relation to sediment-quality guidelines within and outside of Areas of Concern, Lake Erie–Lake saint Clair Drainages, 1990-97.
36 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

arsenic, lindane, zinc, cadmium, lead, and copper 

ranged from 1 to less than 10 times their PEL’s. Most 

of the elevated concentrations of PAH’s were reported 

in Williams Ditch, a tributary to the Ottawa River, but 

elevated PAH’s were also found in the main stem. 

In the River Rouge in Michigan, maximum concentrations of 12 contaminants were greater than their 

PEL’s. Maximum concentrations of anthracene and 

phenanthrene were 115 and 147 times their PEL’s, 

respectively. Maximum concentrations of total PAH’s, 

benz[a]anthracene, total PCB, chrysene, and 

benzo[a]pyrene ranged from 10 to less than 100 times 

their PEL’s. Maximum concentrations of mercury, 

zinc, cadmium, lead, and copper ranged from 1 to less 

than 10 times their PEL’s. Elevated total PCB, mercury, zinc, cadmium, lead, and copper were a problem 

throughout the area, but most of the contamination 

was noted in the lower reach near the mouth of the 

River Rouge.

In the Clinton River in Michigan, maximum 

concentrations of 15 contaminants were greater than 

their PEL’s. The highest concentrations of total PAH’s 

were 138 to 722 times the PEL. The maximum concentrations of anthracene, phenanthrene, 

benz[a]anthracene, total PCB’s, chrysene, 

benzo[a]pyrene, total chlordane, and lindane ranged 

from 10 to less than100 times their PEL’s. The maximum concentrations of mercury, arsenic, zinc, cadmium, lead, and total DDT ranged from 1 to less than 

10 times their PEL’s. The worst bed-sediment contamination from total PAH’s was in the headwaters of the 

Clinton River. The 14 other contaminants of concern 

with concentrations that exceeded PEL’s were elevated 

throughout the study area; however, maximum conTable 5. Ten river basins with highest level and frequencies of bed-sediment contamination in the Lake Erie-Lake 

Saint Clair Drainages, 1990–97

[Rankings based on the degree and frequency that bed-sediment samples exceed Probable Effect Level (PEL) guidelines;z = concentration in at least one 

sample exceeded 100 times the contaminant’s PEL;z = concentration in at least one sample exceeded 10 times the contaminat’s PEL; z = concentration in at 

least one sample exceeded the contaminant’s PEL; z = concentrations in all samples were below the contaminant’s PEL]

River basin names listed in 

degree of exceedance of PEL’s

Contaminants of Concern listed in frequency of exceedance of PEL’s

Anthracene

Total PAH

Phenanthrene

Total PCB

Benz[a]anthracene

Chrysene

Benzo[a]pyrene

Total Chlordane

Mercury

Lindane

Dieldrin/aldrin

Lead

Zinc

Cadmium

Arsenic

Copper

Total DDT

Ottawa River at Toledo, Ohio z z z z z z z z z z z z z z z z z

River Rouge, Mich. z z z z z z z z z z z z z z z z z

Clinton River, Mich z z z z z z z z z z z z z z z z z

Detroit River, Mich. z z z z z z z z z z z z z z z z z

River Raisin, Mich. z z z z z z z z z z z z z z z z z

Lake St. Clair, Mich. z z z z z z z z z z z z z z z z z

Cuyahoga River, Ohio z z z z z z z z z z z z z z z z z

Maumee River, Ohio z z z z z z z z z z z z z z z z z

Little Cuyahoga River, Ohio z z z z z z z z z z z z z z z z z

Ashtabula River, Ohio z z z z z z z z z z z z z z z z z
Summary 37

centrations were most frequently found in the lower 

reach and near the mouth of the Clinton River.

In the Detroit River in Michigan, maximum 

concentrations of 13 contaminants were greater than 

their PEL’s. The maximum concentration of 

anthracene was 147 times the PEL, and the maximum 

concentrations of total PAH, phenanthrene, 

benz[a]anthracene, total PCB, chrysene, 

benzo[a]pyrene, and mercury ranged from 10 to less 

than 100 times their PEL’s. The maximum concentrations of arsenic, zinc, cadmium, lead, and copper 

ranged from 1 to less than 10 times their PEL’s. The 

highest bed-sediment contamination was found in the 

downstream reach of the Detroit River, known as the 

Trenton Channel.

In the River Raisin in Michigan, maximum concentrations of 12 bed-sediment contaminants were 

greater than their PEL’s. The highest concentrations of 

total PCB’s ranged from 191 to 145,000 times the 

PEL, and the maximum concentrations of total PAH, 

phenanthrene, benz[a]anthracene, chrysene, 

benzo[a]pyrene, mercury, arsenic, zinc, cadmium, 

lead, and copper ranged from 1 to less than 10 times 

their PEL’s. The worst bed-sediment contamination 

was from total PCB’s, near the mouth of the River Raisin. The 11 other contaminants of concern were found 

mostly in the lower reach near the mouth of the River 

Raisin. The exception was arsenic, which was found at 

concentrations greater than the PEL in the headwater 

area of the River Raisin.

In Lake Saint Clair in Michigan, maximum concentrations of 12 contaminants were greater than their 

PEL’s. The maximum concentrations of total PCB’s 

and total chlordane ranged from 11.7 to 27.3 times 

their PEL’s, and maximum concentrations of 

anthracene, phenanthrene, benz[a]anthracene, chrysene, benzo[a]pyrene, mercury, cadmium, and lead 

ranged from 1 to less than 10 times their PEL’s. The 

worst contamination was found in bed sediments 

along the western shoreline of Lake Saint Clair. 

In the Cuyahoga River in Ohio, maximum concentrations of 14 contaminants were greater than their 

PEL’s. The highest concentrations of total PAH’s 

ranged from 10 to 11.1 times the PEL and the maximum concentration of mercury was 12.5 times the 

PEL. Maximum concentrations of anthracene, phenanthrene, benz[a]anthracene, total PCB, chrysene, 

benzo[a]pyrene, total chlordane, arsenic, dieldrin plus 

aldrin, zinc, cadmium, lead, and copper ranged from 1 

to less than 10 times their PEL’s. The worst bed-sediment contamination was from total PAH, found in 

some of the tributaries to the main stem near Cleveland and at Akron, Ohio. The 13 other contaminants of 

concern that exceeded their PEL’s were found at many 

locations throughout the Cuyahoga River from Akron 

to Cleveland, Ohio. In the Little Cuyahoga River near 

Akron, Ohio, concentrations of mercury, phenathrene, 

benz[a]anthracene, chrysene, benzo[a]pyrene, total 

chlordane, zinc, and lead were greater than their 

PEL’s.

In the Maumee River, which drains parts of 

Michigan, Indiana, and Ohio, maximum concentrations of 13 contaminants were greater than their PEL’s. 

The maximum concentration of total PAH was 10.6 

times the PEL. Maximum concentrations of 

anthracene, phenanthrene, benz[a]anthracene, total 

PCB, chrysene, benzo[a]pyrene, total chlordane, 

arsenic, lindane, zinc, cadmium, and lead ranged from 

1 to less than 10 times their PEL’s. Most of the organic 

contaminants were found in the lower reach near the 

mouth at Toledo, Ohio, and downstream from Fort 

Wayne, Indiana. Trace-metal contamination appears to 

be widespread downstream from many of the urban 

centers of various sizes throughout the study area.

In the Ashtabula River, the maximum concentrations of eight contaminants were greater than their 

PEL’s. The maximum concentration of phenanthrene 

was 10.1 times the PEL, and maximum concentrations 

of anthracene, benz[a]anthracene, chrysene, 

benzo[a]pyrene, total chlordane, arsenic, and zinc 

ranged from 1 to less than 10 times their PEL’s. All the 

bed-sediment contaminants were found near or at the 

mouth of the Ashtabula River.

Summary

This report describes the occurrence and distribution 

of contaminants of concern in streambed sediments in 

the Lake Erie–Lake Saint Clair Drainages, compares 

these bed-sediment contaminant concentrations to 

guidelines that indicate concentrations either acutely 

or chronically toxic to aquatic macroinvertebrates, and 

discusses the extent and magnitude of contamination 

within Areas of Concern (AOC’s) relative to other 

areas. The study that produced this report used four 

large databases that cover parts of the Lake Erie–Lake 

Saint Clair Drainages: the National Sediment Inventory (NSI), Ohio Sediment data Inventory (OSI), 

USEPA-Fully Integrated Environmental Locational 

Decision Support system (FIELDS) database, and the 
38 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

USGS-National Water-Quality Assessment Program 

(NAWQA) sediment data. Only bed-sediment samples 

collected during 1990–1997 (in the top 5 inches of 

sediment) in the United States part of the Lake Erie–

Lake Saint Clair Drainages were evaluated to reflect 

recent U.S. conditions. 

The data are compared to three freshwater bedsediment-quality guidelines used in the Great Lakes 

area: Ontario Ministry of Environment guidelines for 

the protection and management of Canadian freshwater sediments; USEPA guidelines for Great Lakes sediments; and Environment Canada and the Great Lakes 

guidelines for ecosystems throughout Canada and the 

Great Lakes Basin. The location and concentration 

range of selected contaminants of concern are mapped 

in this report, and each compound is discussed as to its 

toxicity to biota according to these regional bed-sediment guidelines. 

The larger the stream, the more likely it was to 

be contaminated by one or more organic-chemical 

compounds or trace metals. This study showed that 

surficial bed sediments in streams within “Areas of 

Concern” (AOC’s), previously identified by the International Joint Commission, contained the highest percentage of detections of the organic compounds 

chlordane, total PCB, and various PAH’s and were 

most likely to have contaminant concentrations greater 

than Probable Effect Level (PEL) and Severe Effect 

Level (SEL) guidelines. The highest concentrations of 

anthracene, total PAH, phenanthrene, 

benz[a]anthracene, total PCB, chrysene, 

benzo[a]pyrene, and (or) chlordane in bed sediment 

were in the Clinton River, Detroit River, River Raisin, 

and River Rouge AOC’s, in Michigan; and in the 

Maumee River and Cuyahoga River AOC’s, in Ohio. 

The dominant factor influencing bed-sediment tracemetal concentrations of cadmium, copper, lead, and 

mercury appeared to be urban land use in the basin of 

the receiving stream. The study indicated a fairly high 

probability that trace-metal concentrations will exceed 

the PEL and SEL guidelines in many principal streams 

or tributaries to Lake Saint Clair and Lake Erie that 

pass through major urban centers. 

Exceedance of PEL’s and SEL’s for total DDT, 

dieldrin, hexachlorocyclohexane, and lindane concentrations were found in streams draining urban and 

agricultural areas throughout the Lake Erie–Lake Saint 

Clair Drainages; indicating the influence of both types 

of land use. Mirex and hexachlorobenzene were not 

found to be a significant problem in the basin; however, lower detection limits would improve confidence 

in the assessment of hexachlorobenzene. Because the 

concentrations of some trace-metals in soil vary naturally, depending on the type of surficial and bedrock 

materials they are derived from, distinguishing the primary sources of arsenic and zinc may be complicated.

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management strategy: Allen, Herbert E., ed., Metal 

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Daher, Shannon, 1998, Lake Erie Lakewide Management 

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Fox, Catherine, 1994, The National Sediment Inventory, 

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Fox, Richard, and Tuchman, Marc, 1996, The assessment 

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Furlong, E.T., Vaught, D.G., and Merten, L.M., Foreman, 

W.T., and Gates, P.M., 1996, Methods of analysis by 

the U.S. Geological Survey National Water Quality 

Laboratory-Determination of semivolatile organic 

compounds in bottom sediment by solvent extraction, 

gel permeation chromatographic fractionation, and 

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719, 67 p.

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Columbus, Ohio, The Ohio State University Center for 

Lake Erie Area Research, CLEAR Technical Report 

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470 p.

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40 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

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Appendix A 41

 Appendix A

Methods of sample collection, analysis, quality assurance, and quality control

Table A1. Chemical class, number of agencies providing databases, and number of analyzing laboratories 

contributing sediment-quality data, 1990–97

Table A2. Summary of sample-collection methods

Table A3. Summary of sample preparation and analysis methods

Table A4. Summary of quality-assurance programs and quality-control procedures
42 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Methods of sample collection, analysis, quality 

assurance, and quality control

Seven public agencies collected and provided the data 

used in this report, and 15 laboratories analyzed and 

reported sample results. (see section on “Sampling 

Agencies and Analyzing Laboratories.”) A summary 

of data classes collected and reported by these entities 

is given in table A1. Aquatic sediment-collection 

methods varied with the depth, location, and texture of 

sediments (table A2). Shallow areas in streams were 

sampled with stainless steel spoons or scoops, Petit 

Ponar or Ponar dredges, or hand corers. Deeper samples were collected with Ponar dredges or with core 

samplers. All samples for subsequent analysis of 

organic contaminants were handled with cleaned stainless steel or Teflon-coated utensils and stored in precleaned glass jars with Teflon lid liners. Samples for 

trace metals were collected and processed with 

polypropylene sieves and stored in plastic jars.

Most protocols stipulated that samples be sieved 

or otherwise processed in the field to eliminate coarse 

material and debris. After removal of coarse material, 

samples were subsequently homogenized by thoroughly mixing or stirring with a clean utensil or with a 

blender. After collection and processing, all samples 

were chilled or frozen until analysis. For organic compounds, if samples were chilled, analysis was completed within 2 to 40 days. If samples were frozen, 

analysis for organic compounds was completed within 

1 year. For trace metals, analysis was completed 

within 1 to 6 months. In the case of mercury, samples 

were analyzed within 30 days.

All contaminant concentrations in bed sediments are reported as dry weight, in milligrams per 

kilogram. Analysis of trace metals followed methods 

published by the U.S. Environmental Protection 

Agency (1979, 1993a, 1998); Foreman and others 

(1995); Furlong and others (1996); or the American 

Public Health Association and others (1995) for analysis of aquatic bed sediments or solid-waste materials 

(table A3). Subsamples were dried and weighed to 

determine percent moisture. Trace-element samples 

were digested prior to analysis with a strong acid, 

either nitric acid or hydrochloric acid, or a combination of both. Results obtained from acid-digested samples are considered “total recoverable trace metals.” 

For trace-element samples analyzed by XRF (Xray fluorescence spectroscopy), no digestion was 

done. For USGS samples, acid digestion was done 

with hydrofluoric acid followed by AAS (Atomic 

Absorption Spectroscopy), ICP (Inductively Coupled 

Plasma Emission Spectroscopy), or ICP-MS (mass 

spectroscopy). Results obtained by XRF or following 

hydrofluoric acid digestion are considered “total trace 

metals” (Smith and others, 1995) and represent a more 

complete measure of trace-element composition of 

sediments than those for sediments digested with nitric 

or nitric and hydrochloric acid. Results obtained using 

XRF are approved for use by USEPA in the SW-846 

(Solid Waste Methods, U.S. Environmental Protection 

Agency, 1998) along with the more commonly used 

AAS and ICP methods. Only mercury samples analyzed by the cold vapor-AAS method were used for 

this report. 

Analysis of organochlorine and semivolatile 

compounds was done after solid phase/solvent or 

soxhlet extraction and sample cleanup to remove sample-matrix interferences. Instrumental analysis for 

determination of organochlorine compounds was done 

by dual capillary column GC (gas chromatography) or 

by GC/MS (gas chromatography/mass spectrometry). 

Instrumental analysis of PAH’s and other semivolatile 

compounds was done by GC with FID (flame ionization detector) or GC/MS. One laboratory used immunoassay methods for PCB’s and PAH’s. Although not 

commonly used, these methods are approved and documented for analysis of soils and sediments by USEPA 

as part of SW-846 (U.S. Environmental Protection 

Agency, 1998). Samples may have been analyzed for 

concentrations of total organic carbon as well as trace 

organic contaminants. Samples for this report were not 

normalized against individual results for concentrations of total organic carbon. 

Quality-assurance/quality-control (QA/QC) 

methods were used by each collecting agency and analyzing laboratory (table A4). The elements of a quality-assurance and quality-control program deemed to 

be the most important to this interpretive report are (1) 

the documentation and use of a QA/QC plan, (2) documentation of methods of collection, field preparation, 

transport, and analysis, and (3) evaluation of precision, 

bias, and overall accuracy through the use of various 

quality-control procedures. All data accepted for 

inclusion in this report came from programs or 

projects that had QA/QC plans in place and used quality-control procedures to evaluate data quality, as indicated in tables A3-A4.
Appendix A 43

Table A1. Chemical class, number of agencies providing databases, and number 

of analyzing laboratories contributing sediment-quality data,1990–97

Table A2. Summary of sample-collection methods

[USEPA, U.S. Environmental Protection Agency; USGS, U.S. Geological Survey; USACE, U.S. Army Corps of Engineers; 

MDNR, Michigan Department of Natural Resources; NYSDEC, New York State Department of Environmental Conservation; 

Ohio EPA, Ohio Environmental Protection Agency; RPO, Rouge Program Office]

1 U.S. Environmental Protection Agency, 1993a.

2 Shelton and Capel, 1994.

3 Nielson and Sanders, 1983.

4

 Myers and others, 1994.

5 Ohio Environmental Protection Agency, 1995, 1997.

6 Smith and others, 1995.

Class of chemical compound Number of collecting 

and reporting agencies

Number of analyzing 

laboratories

Organochlorine pesticides 4 8

Polycyclic aromatic hydrocarbons 5 9

Polychlorinated biphenyls 6 11

Trace metals 6 12

Total 7 15

Collection methods

Collecting agency

USEPA1 USGS2 USACE/

MDNR3

NYS

DEC4

Ohio

EPA5 RPO6

Grab sample(s) X X X X

Composite sample X X

Petit ponar X

Ponar X X

Hand core X

Vibracore X X

Van Veen X
44 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Table A3. Summary of sample preparation and analysis methods

[n/a, not applicable; P, sample preparation; A, sample analysis; D-nh, digestion with nitric and hydrochloric acids; 

D-f, digestion with hydrofluoric acid; Ex, Extraction; SE, solvent extraction; SoE, soxhlet extraction; C, cleanup procedure; F, fluorosil cleanup; S, 

elemental sulfur cleanup; Me-NaS, methanol-sodium sulfate extraction; SG, silica gel cleanup; ICP, inductively coupled plasma emission spectrocopy; 

ICP/MS, inductively coupled plasma emission spectroscopy-mass spectrometry; GP, gel permeation chromatography; GC-ECD, gas chromatographyelectron capture detection; GC/FID, gas chromatography-flame ionization detection; GC-MS, gas chromatography-mass spectrometry; XRF, X-ray 

fluorescence spectrometry; I, immunoassay; U.S. Environmental Protection Agency, 1993a;

USEPA, U.S. Environmental Protection Agency; USGS, U.S. Geological Survey; USACE, U.S. Army Corps of Engineers; 

MDNR, Michigan Department of Natural Resources; NYSDEC, New York State Department of Environmental Conservation; Ohio EPA, Ohio

Environmental Protection Agency; RPO, Rouge Program Office]

01

 U.S. Environmental Protection Agency, 1994.

02 U.S. Environmental Protection Agency, 1998.

03

 U.S. Environmental Protection Agency, 1979.

04 Arbogast, 1990. 05 Foreman and others, 1995. 06 Furlong and others, 1996. 07 U.S. Environmental Protection Agency, 1993b. 08 Ohio Environmental Protection Agency, 1995. 09 American Public Health Association and others, 1995. 10 Myers and others, 1994. 11 Rouge Program Office, 1995.

12 Nielson and Sanders, 1983.

Organization

Methods of sample preparation and analysis

Trace elements Mercury

PCB’s and 

organochlorine 

pesticides

Semivolatile 

compounds

P A P A Ex C A Ex C A

USEPA1,2,3

D-nh ICP D

AACV SoE F,SGCECD SoE SGGC/

FID

USGS4,5,6

D-f

ICP/

MS D

AACV SoE GPGCECD SE GPGC/

MS

USACE/

MDNR1,2,7 D AAS D

AACV SoE GPGCMS SoE GPGC/

MS

NYSDEC1,2,3,10

D-nh AAS D-nh

AACV n/a n/a n/a n/a n/a n/a

Ohio EPA2,3,8,9

D ICP D

AACV SE F,SGCMS SE SGGC/

MS

RPO1,2,11

n/a

XRF12

n/a n/a n/a n/a

I

1 MeNaS n/a

I

1
Appendix A 45

Table A4. Summary of quality-assurance programs and quality-control procedures

[Y, yes; QA, quality assurance; CRM, Certified Reference Material; SRM, Standard Reference Material; USGS, U.S. Geological Survey; USACE,

U.S. Army Corps of Engineers; MDNR, Michigan Department of Natural Resources; NYSDEC, New York State Department of Environmental

Conservation; Ohio EPA, Ohio Environmental Protection Agency; RPO, Rouge Program Office]

1

 Schumaker, 1994.

2

 Arbogast, 1990.

3 Jones, 1987.

4 Michigan Department of Natural Resources, 1994.

5 Myers and others, 1994.

6 Ohio Environmental Protection Agency, 1995.

7 Ohio Environmental Protection Agency, 1997.

8 Rouge Program Office, 1994.

Organization

Quality-assurance plans and quality-control procedures

QA 

plan

Analysis 

frequency of 

replicate 

samples 

(percent)

Analysis 

frequency of 

laboratory 

blanks 

(percent)

Analysis 

frequency of 

laboratory 

matrix or 

surrogate 

spike samples

Other 

qualitycontrol 

checks

USEPA1

Y 20 Daily 5

SRM CRM

USGS2,3 Y 10 5 10 SRM

USACE/MDNR1,4

Y 15 Daily 5

SRM, CRM

NYSDEC5 Y 7 10-15 7 SRM

Ohio EPA6,7 Y 5-10 Daily 1-5 SRM

RPO8 Y 5 5 5 SRM
46 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Appendix B

Figures B1-B20–Graphs showing probability distributions of concentrations and detection limits

for streambed and lakebed sediments in relation to sediment-quality guidelines, Lake Erie–Lake

Saint Clair Drainages, 1990–97.
Appendix B 47

0.89

0.089

0.0089

0.0045

0.00001

0.00010

0.00100

0.01000

0.10000

1.00000

10.00000

99.99% 10.00% 1.00% 0.10%

TOTAL CHLORDANE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; chlordane not found

Chlordane found above detection limits

 100 times probable effect limit

 10 times probable effect level

Probable effect level (0.0089 mg/kg)

Threshold effect level (0.0045 mg/kg)

Figure B1. Probability distribution of total chlordane concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

4.45

0.007

0.001

0.010

0.100

1.000

10.000

100.000

99.99% 10.00% 1.00% 0.10%

TOTAL DDT CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; DDT not found

Total DDT found above detection limits

Probable effect level (4.45 mg/kg)

Threshold effect level (0.007 mg/kg)

Figure B2. Probability distribution of total DDT concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.
48 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

0.0667

0.00667

0.00285

0.0001

0.0010

0.0100

0.1000

1.0000

99.99% 10.00% 1.00% 0.10%

DEILDRIN CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; deildrin not found

Deildrin found above detection limits

 10 times probable effect level

Probable effect level (0.00667 mg/kg)

Threshold effect level (0.00285 mg/kg)

Figure B3. Probability distribution of dieldrin concentrations and detections limits for streambed and lakebed 

sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

2.4

0.24

0.02

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

99.99% 10.00% 1.00% 0.10%

HEXACHLOROBENZENE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; hexachlorobenzene not found

Hexachlorobenzene found above detection limits

 10 times severe effect level

Severe effect level (0.24 mg/kg)

Lowest effect level (0.02 mg/kg)

Figure B4. Probability distribution of hexachlorobenzene concentrations and detection limits for streambed and lakebed

sediments in relation to aquatic-life criteria, Lake Eire–Lake Saint Clair Drainages, 1990–97.
Appendix B 49

Figure B5. Probability distribution of total hexachlorocyclohexane (BHC) concentrations and detection limits for streambed 

and lakebed sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

0.138

0.0138

0.00138

0.00094

0.0001

0.0010

0.0100

0.1000

1.0000

99.99% 10.00% 1.00% 0.10%

LINDANE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; lindane not found

Lindane found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (0.00138 mg/kg)

Threshold effect level (0.00094 mg/kg)

Figure B6. Probability distribution of lindane (γ-hexachlorocyclohexane) concentrations and detection limits for streambed 

and lakebed sediments inrelation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

0.12

0.003

0.0001

0.0010

0.0100

0.1000

1.0000

99.99% 10.00% 1.00% 0.10%

TOTAL BHC CONCENTRATIONS,IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; BHC not found

BHC found above detection limits

Severe effect level (0.12 mg/kg)

Lowest effect level (0.003 mg/kg)
50 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Figure B8. Probability distribution of total PCB concentrations and detection limits for streambed and lakebed sediments in 

relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

1.3

0.007

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

99.99% 10.00% 1.00% 0.10%

MIREX CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; mirex not found

Severe effect level (1.30 mg/kg)

Lowest effect level (0.007 mg/kg)

Figure B7. Probability distribution of total mirex concentrations and detection limits for streambed and lakebed 

sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990-97.

27.7

2.77

0.277

0.0341

0.001

0.010

0.100

1.000

10.000

100.000

1,000.000

10,000.000

100,000.000

99.99% 10.00% 1.00% 0.10% 0.01%

TOTAL PCB CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; PCB not found

PCB found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (0.277 mg/kg)

Threshold effect level (0.0314 mg/kg)
Appendix B 51

340

34

3.4

0.26

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

1,000.0000

10,000.0000

99.99% 10.00% 1.00% 0.10%

TOTAL PAH CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; PAH's not found

Total PAH's found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (3.40 mg/kg)

Threshold effect level (0.260 mg/kg)

Figure B9. Probability distribution of total PAH concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

17

1.7

0.17

0.01

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

99.99% 10.00% 1.00% 0.10%

Specified detection limits: anthracene not found

Anthracene found above detection limits

100 times probable effect level

10 times probable effect level

Probable effect level (0.17 mg/kg)

Threshold effect level (0.01 mg/kg)

ANTHRACENE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Figure B10. Probability distribution of anthracene concentrations and detection limits for streambed and lakebed sediments 

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.
52 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

38.5

3.85

0.385

0.0317

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

1,000.0000

99.99% 10.00% 1.00% 0.10%

BENZ[

a]ANTHRACENE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Speified detection limits; benz[a]anthracene not found

Benz[a]anthracene found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (0.385 mg/kg)

 Threshold effect level (0.0317 mg/kg)

Figure B11. Probability distribution of benz[a]anthracene concentrations and detection limits for streambed and lakebed

sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

78.2

7.82

0.782

0.0319

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

1,000.0000

99.99% 10.00% 1.00% 0.10%

BENZ0[

a]PYRENE CONCENTRATION,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; benzo[a]pyrene not found

Benzo[a]pyrene found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (0.782 mg/kg)

Threshold effect level (0.0319 mg/kg)

Figure B12. Probability distribution of benzo[a]pyrene concentrations and detection limits in streambed and lakebed

sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97. 
Appendix B 53

86.2

8.62

0.862

0.0571

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

1,000.0000

99.99% 10.00% 1.00% 0.10%

CHRYSENE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; chrysene not found

Chrysene found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (0.862 mg/kg)

Threshold effect level (0.0571 mg/kg)

Figure B13. Probability distribution of chysene concentrations and detection limits for streambed and lakebed sediments in 

relation to aquatic-life croteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

51.5

5.15

0.515

0.0419

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

1,000.0000

99.99% 10.00% 1.00% 0.10%

PHENANTHRENE CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; phenanthrene not found

Phenanthrene found above detection limits

 100 times probable effect level

 10 times probable effect level

Probable effect level (0.515 mg/kg)

Threshold effect level (0.0419 mg/kg)

Figure B14. Probability distribution of phenanthrene concentrations and detection limits for streambed and lakebed 

sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.
54 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

170

17

5.9

1.000

10.000

100.000

1,000.000

99.99% 10.00% 1.00% 0.10%

ARSENIC CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; arsenic not found

Arsenic found above detection limits

 10 times probable effect level

Probable effect level (17 mg/kg)

Threshold effect level (5.9 mg/kg)

Figure B15. Probability distribution of arsenic concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

3.53

0.596

0.010

0.100

1.000

10.000

100.000

99.99% 10.00% 1.00% 0.10% 0.01%

CADMIUM CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; cadmium not found

Cadmium found above detection limits

Probable effect level (3.53 mg/kg)

Threshold effect level (0.596 mg/kg)

Figure B16. Probability distribution of cadmium concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.
Appendix B 55

197

35.7

0.100

1.000

10.000

100.000

1,000.000

99.99% 10.00% 1.00% 0.10%

COPPER CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; copper not found

Copper found above detection limits

Probable effect level (197 mg/kg)

Threshold effect level (35.7 mg/kg)

Figure B17. Probability distribution of copper concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria. Lake Erie–Lake Saint Clair Drainages, 1990–97.

91.3

35

1.000

10.000

100.000

1,000.000

99.99% 10.00% 1.00% 0.10% 0.01%

LEAD CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; lead not found

Lead found above detection limits

Probable effect level (91.3 mg/kg)

Threshold effect level (35 mg/kg)

Figure B18. Probability distribution of lead concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.
56 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

4.86

0.486

0.174

0.0001

0.0010

0.0100

0.1000

1.0000

10.0000

100.0000

99.99% 10.00% 1.00% 0.10% 0.01%

TOTAL MERCURY CONCENTRATIONS,

IN MILLIGRAMS PER KILOGRAM

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Specified detection limits; mercury not found

Mercury found above detection limits

 10 times probable effect level

Probable effect level (0.486 mg/kg)

Threshold effect level (0.174 mg/kg)

Figure B19. Probability distribution of mercury concentrations and detection limits for streambed and lakebed sediments

sediments in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.

315

123

0.100

1.000

10.000

100.000

1,000.000

10,000.000

99.99% 10.00% 1.00% 0.10%

ZINC CONCENTRATIONS,

IN MILLIGRAMS PER KILOMETER

PERCENTAGE OF VALUES EXCEEDING A GIVEN CONCENTRATION

Zinc found above detection limits

Probable effect level (315 mg/kg)

Threshold effect level (123 mg/kg)

Figure B20. Probability distribution of zinc concentrations and detection limits for streambed and lakebed sediments

in relation to aquatic-life criteria, Lake Erie–Lake Saint Clair Drainages, 1990–97.
Appendix C 57

Appendix C

Development of bed-sediment-quality guidelines in Canada and the United States

Sediment Effect Concentrations–Classifying Toxicity of United States Great Lakes Sediment

Sediment Quality Assessment Values for Ecosystems in Canada and the Great Lakes 
58 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Development of Bed-Sediment-Quality Guidelines In Canada and the United States

In 1992, the Ontario Ministry of Environment developed guidelines for evaluating sediments throughout 

Ontario (Persaud and others, 1993) that replaced the 

Open Water Disposal Guidelines (published by the 

Ministry in 1976). The PSQG (Provincial Sediment 

Quality Guidelines) are intended to provide guidance 

during decision making in relation to sediment issues, 

ranging from prevention to remedial action (Persaud 

and others, 1993). The PSQG’s were developed for the 

protection of aquatic biological resources, particularly 

organisms that are directly effected by contaminated 

sediments; namely the sediment-dwelling (benthic) 

species.

These guidelines are designed to help environmental managers determine (1) when sediments may 

be considered clean, (2) what concentrations of contamination are acceptable for short periods of time 

while the source of the contamination is being controlled and cleanup plans are being developed, and (3) 

what concentrations of contamination are severe 

enough to consider the possibility of either removing 

the sediment or capping it with a layer of cleaner sediment.

The Ontario guidelines define three levels of 

ecotoxic effects and are based on the chronic, longterm effects of contaminants on benthic organisms. 

These levels are (1) NEL (No Effect Level) at which 

no toxic effects have been observed on aquatic organisms, (2) LEL (Lowest Effect Level) indicating a level 

of sediment contamination that can be tolerated by the 

majority of benthic organisms, and (3) SEL (Severe 

Effected Level) indicating the level at which pronounced disturbance of the sediment-dwelling community can be expected. 

The NEL guidelines were developed by use of 

the partitioning approach, by which existing criteria 

such as a water quality or tissue residue criteria can be 

considered as virtual no-effect values. The approach is 

limited by its assumption of a single route of exposure 

for aquatic organisms and its restriction to the nonpolar organics. The NEL guidelines cannot be calculated 

for trace metals and polar organic compounds. 

The LEL (Lowest Effect Level) is the concentration at which actual ecotoxic effects become apparent. It is derived using field-based data on the cooccurrence of sediment concentrations and benthic 

species. The LEL is calculated by means of a two-step 

screening-level concentration method. The first step is 

to calculate the screening-level concentration of each 

chemical for a large number of species (at least 10 for 

each chemical) and then plot the frequency distribution of the contaminant concentrations over all sites 

where the species is present (at least 10 sites). The 

90th percentile of this distribution is then taken as the 

species screening-level concentration. In the second 

step, the species screening-level concentrations for 

each species are plotted as a frequency distribution, 

and the 5th percentile is interpolated from this distribution. This 5th percentile concentration represents 

the LEL concentration that 95 percent of the species 

can tolerate (table 2 in the main text). 

The SEL (Severe Effect Level) represents contaminant concentrations in bed sediment that could 

potentially eliminate most of the benthic organisms. It 

is obtained by calculating the 95th percentile of the 

screening-level concentration as described for LEL’s 

(the concentration below which 95 percent of all species screening-level concentrations fall). This concentration value represents the SEL concentration that 95 

percent of the species cannot tolerate. 

Persaud and others (1993) published the LEL 

and SEL guideline concentrations for trace metals, 

nutrients, and polar organics in parts per million dry 

weight. For nonpolar organics; however, many compounds tend to adsorb to organic carbon in suspended 

and bed sediments, reducing bioavailability (Scudder 

and others, 1997). Persaud and others (1993) suggested that their SEL concentration guideline for nonpolar organics be converted to bulk sediment values by 

multiplying by the actual total organic carbon (TOC) 

concentration of the sediments (to a maximum of 10 

percent). For this report, we took the conservative 

approach suggested by Smith and others (1996) and 

assumed 1 percent TOC to determine SEL guideline 

values. If however, the percentage of TOC in the sample is known to be greater then 1 percent, then nonpolar organic SEL guideline values should be adjusted 

upward accordingly. 

Sediment Effect Concentrations–Classifying Toxicity 

of United States Great Lakes Sediment

In 1992, the USEPA proposed a national strategy to 

manage the problems of contaminated bed sediments 

at numerous sites throughout much of the United 

States (Ingersoll and others, 1996). In the Great Lakes 

area, the concern was that these sediments pose a 

health risk to humans and the ecosystem as a whole. 
Development of Bed-Sediment-Quality Guidelines In Canada and the United States 59

Yet, much uncertainty remained about the concentrations and spatial distribution of these contaminants in 

aquatic sediments, especially in harbors and other disturbed areas. The need to map contaminant deposits 

accurately and to characterize them became apparent 

to the USEPA, which established the ARCS (Assessment and Remediation of Contaminated Sediments) 

program to help address the contaminated sediment 

problem at the 42 Great Lakes AOC’s (Ross and others, 1992). The program was administered out of the 

USEPA Great Lakes National Program Office in Chicago, Illinois.

As part of the ARCS program (Ross and others, 

1992; and Fox and Tuchman, 1996), whole-sediment 

toxicity tests were done by several contracted 

researchers during 1993-96 (Ingersoll and others, 

1996) using the amphipod Hyalella azteca and the 

midge Chironomus riparius in sediments collected 

from various Great Lakes AOC’s and additional sites 

across the United States in order to make the database 

as robust as possible. Ingersoll and others (1996) 

described the procedures for calculating and evaluating SEC (sediment effect concentrations) with this 

data set. 

SEC’s were determined by classifying chemicals measured in each sample in terms of their association with the observed toxicity. Each of the chemicals 

in the toxic samples was classified as an “effect” or 

“no concordance,” depending on whether the ratio of 

the concentration in the sample to the mean concentration in the nontoxic samples was > 1 or < 1. Concentrations of chemicals in nontoxic samples were 

designated as “no effects.” Samples designated with 

the no concordance descriptor were also included with 

no-effect samples for calculation of SEC’s.

Three types of SEC’s were calculated by Ingersoll and others (1996) using the greater than mentioned data: (1) ERL (Effect Range Low) and ERM 

(Effect Range Median), (2) TEL (Threshold Effect 

Level) and PEL (Probable Effect Level), and (3) NEC 

(No Effect Concentration). They were able to calculate 

23 SEC’s primarily for total trace metals, simultaneously extracted metals, PCB’s, and PAH’s (table 2 in 

main text). The ranges of concentrations in their sediment database were too narrow to adequately evaluate 

SEC’s for butyltins, methyl mercury, polychlorinated 

dioxins and furans, or chlorinated pesticides. 

 ERL’s and ERM’s were determined from concentrations observed or predicted by different methods 

to be associated with effects, sorted in ascending 

order, and the lower 15th percentile (or ERL) and 50th 

percentile (or ERM) effect concentrations were then 

calculated. An ERL was defined as the concentration 

of a chemical in sediment below which adverse effects 

were rarely observed or predicted among sensitive 

species. An ERM was defined as the concentration of 

a chemical in sediment greater than which effects are 

frequently or always observed or predicted among 

most species.

In addition, the 50th-percentile concentration 

(or NERM, No Effect Range Median) and the 85thpercentile concentrations (or NERH, No Effect Range 

High) of the “no-effects” data set were calculated. The 

TEL’s were calculated as the geometric mean of the 

ERL and NERM, whereas the PEL’s were calculated 

as the geometric mean of the ERM and NERH. The 

geometric mean was used rather than the arithmetic 

mean because the two data sets are not normally distributed. The NEC (No Effect Concentration) was calculated as the maximum concentration of a chemical 

in a sediment that did not significantly adversely affect 

the particular response (for example, survival, growth, 

or maturation) compared to the control.

 The work by Ingersoll and others (1996) also 

showed that their calculated ERL’s and ERM’s are 

generally as reliable as paired calculated TEL’s and 

PEL’s at classifying toxic and nontoxic samples. In 

addition, they determined that SEC’s calculated from 

sediment concentrations normalized to TOC (total 

organic carbon) concentrations did not improve the 

reliability compared to SEC’s calculated from dryweight concentrations. Therefore, all values of Ingersoll and others (1996) have been reported as dryweight concentrations.

Sediment Quality Assessment Values for Ecosystems 

in Canada and the Great Lakes 

In 1992, the freshwater bed-sediment information in 

the National Oceanic and Atmospheric Administration 

database (Long and Morgan, 1991) was expanded by 

Environment Canada to incorporate additional information available on the toxicity of chemicals in freshwater sediments (Smith and others, 1996). Many large 

data sets, including the screening-level concentration 

data collected and evaluated in Ontario (Persaud and 

others, 1993) and data sets generated through the 

ARCS program (Ingersoll and others, 1996) were integrated into the BEDS (freshwater biological effects 

database for sediments). Other relevant studies available in the published literature also were included. 
60 Areal Distribution and Concentrations of Contaminants of Concern in Surficial Streambed and Lakebed Sediments, Lake Erie–

 Lake Saint Clair Drainages, 1990–97

Overall, 56 publications met all of Smith and others 

screening criteria, (1996) and were used in the development of the freshwater BEDS. Of these, roughly 35 

percent were studies done in the Great Lakes Basin. 

The expanded freshwater database now supports the 

calculation of numerical sediment-quality assessment 

values for a range of chemical substances and will 

continue to form an important part of the Canadian 

sediment-quality guidelines in the future. 

The BEDS sediment quality assessment values (Smith 

and others, 1996) were developed by means of a 

weight-of-evidence approach in which matching biological and chemical data from numerous modeling, 

laboratory, and field studies of freshwater sediments 

were compiled and analyzed. Two assessment values, 

a TEL and a PEL, were derived for 23 substances 

(eight trace metals, six PAH’s, total PCB’s, and eight 

organochlorine pesticides). The two values define 

three ranges of chemical concentrations: those that 

were (1) rarely, (2) occasionally, and (3) frequently 

associated with adverse biological effects. This 

method is being used as a basis for developing 

national sediment-quality guidelines for freshwater 

systems in Canada and sediment-effect concentrations 

as part of the ARCS program in the Great Lakes.

The TEL’s and PEL’s were calculated for those 

chemicals having at least 20 data entries in both the 

effect and the no-effect data sets. The TEL was 

derived by calculating the geometric mean of the 15th 

percentile of the effect data set and the 50th percentile 

of the no-effect data set. This value was intended to 

estimate the concentration of a chemical below which 

adverse biological effects only rarely occurred. The 

PEL was derived by calculating the geometric mean of 

the 50th percentile of the effect data set and the 85th 

percentile of the no-effect data set. The PEL was 

intended to estimate the concentration of a chemical 

greater than which adverse biological effects frequently occurred. Sediment-quality assessment values 

could not be calculated for a number of individual 

PAH’s and other chemicals for which information was 

included in BEDS but for which fewer than 20 effect 

data entries were available. Future expansions of 

BEDS are expected to result in sufficient information 

to calculate assessment values for additional substances, including silver, individual PAH’s and classes 

of PAH’s, individual PCB congeners and formulations, 

pesticides, dioxins, and furans.