U.S. Department of the Interior 

U.S. Geological Survey 

Trace Elements and Synthetic Organic 

Compounds in Streambed Sediment and Fish 

Tissue in the Great and Little Miami River 

Basins, Ohio and Indiana,1990–98 

By Stephanie D. Janosy 

Water-Resources Investigations Report 02–4305 

National Water-Quality Assessment Program 
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

6480 Doubletree Avenue

Columbus, OH 43229-1111

Copies of this report can be purchased from:

U.S.Geological Survey

Branch of Information Services

Box 25286

Denver, CO 80225-0286

Columbus, Ohio

2003
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. 

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 waterquality management and policy. 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. 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. 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 waterquality 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. 

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 water-resource 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 
CONTENTS

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

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

Purpose and scope ....................................................................................................................................................... 2 

Description of the Great and Little Miami River Basins study unit ........................................................................... 2 

Acknowledgments ....................................................................................................................................................... 3 

Study design and methods .................................................................................................................................................... 3 

Sampling procedures ................................................................................................................................................... 3 

Data analysis .............................................................................................................................................................. 5 

Standards and guidelines ............................................................................................................................................ 7 

Sediment and fish-tissue quality ........................................................................................................................................... 11 

Trace elements ............................................................................................................................................................ 12 

Synthetic organic compounds ..................................................................................................................................... 16 

Summary .............................................................................................................................................................................. 24 

References ............................................................................................................................................................................ 25 

Appendix A— Results of a national assessment of mercury contamination of aquatic ecosystems ................................... 28 

Appendix references ............................................................................................................................................................. 28 

ILLUSTRATIONS 

1. Map showing the Great and Little Miami River Basins study unit, Ohio and Indiana. ................................................... 4 

2. Graph showing percentage of sites where trace elements and synthetic organic compounds were detected 

within the Great and Little Miami Rivier Basins, Ohio and Indiana, 1990–98......................................................... 11 

3. Graph showing arsenic concentrations as a function of sediment clay content at the 

Great and Little Miami River Basin study unit sampling locations, Ohio and Indiana, 1998.................................. 13 

4. Graph showing concentrations of selected trace elements at Great and Little Miami River sites 

compared to Canadian Sediment-Quality Guidelines and selected 1991 and 1994 

national NAWQA study units. .................................................................................................................................. 14 

5. Map showing location of streambed-sediment samples exceeding Canadian Sediment-Quality Guideline 

Probable Effect Levels (PELs) and trace-element detections in fish-tissue samples in the 

Great and Little Miami River Basins, Ohio and Indiana, 1990–98. ......................................................................... 15 

6. Graph showing concentrations of selected organochlorine insecticides at Great and Little Miami River Basins 

streambed-sediment sites compared to Canadian Sediment-Quality Guidelines and data from selected 

1991 and 1994 national NAWQA study units. .........................................................................................................17 

7. Map showing location of streambed-sediment samples exceeding Canadian Sediment-Quality Guideline 

Probable Effect Levels (PELs) and fish-tissue samples exceeding New York Fish 

Flesh Criteria (NYFFC) for organochlorine insecticides in the Great and Little Miami River Basins, 

Ohio and Indiana, 1990–98. ..................................................................................................................................... 18 

8. Graph showing concentrations of selected organochlorine insecticides and total polychlorinated biphenyls 

at Great and Little Miami River Basins fish-tissue sites compared to New York Fish Flesh Criteria (NYFFC) 

and selected 1991 and 1994 national NAWQA study units. ..................................................................................... 19 

9. Map showing location of sediment samples exceeding Canadian Sediment-Quality Guideline Probable 

Effect Levels (PELs) and fish-tissue samples exceeding New York Fish Flesh Criteria (NYFFC) 

for polychlorinated biphenyls in the Great and Little Miami River Basins, Ohio and Indiana, 1990–98. ............... 21 

10. Graph showing concentrations of selected semivolatile organic compounds at Great and Little Miami River Basins 

streambed-sediment sites compared to Canadian Sediment-Quality Guideline Probable Effect Levels 

(PELs), and data from selected 1991 NAWQA study units. ..................................................................................... 22 

Contents V
11. Map showing location of streambed-sediment samples exceeding Canadian Sediment-Quality Guideline 

Probable Effect Levels (PELs) for semivolatile organic compounds in the Great and 

Little Miami River Basins, Ohio and Indiana, 1990–98. ......................................................................................... 23 

A1. Graph showing comparison of mercury concentrations in fish-fillet samples in the Great and Little Miami River Basins 

study unit to range and median concentrations from 21 national NAWQA study units. ........................................ 29 

TABLES 

1. Description of sampling sites in the Great and Little Miami River Basins study unit, Ohio and Indiana .......................5 

2. Constituents analyzed for in streambed sediment and fish tissue by the National Water-Quality Assessment Program 6 

3. Maximum number of streambed-sediment and fish-tissue sites per agency incorporated for analyses .......................... 7 

4. Canadian Sediment Quality Guidelines and New York Fish Flesh Criteria for trace elements, 

organochlorine insecticides, total polychlorinated biphenyls, and semivolatile organic compounds 

including common sources, uses, and examples of potential adverse effects to wildlife ........................................ 8 

5. Particle-size distribution and organic-carbon concentrations at Great and Little Miami River Basins 

streambed-sediment sampling sites, Ohio and Indiana, 1998 ................................................................................. 12 

A1. Mercury concentrations in fish fillets, bed sediment, and surface water at selected sampling locations 

in the Great and Little Miami River Basins ............................................................................................................ 29 

VI Contents
CONVERSION FACTORS AND ABBREVIATIONS 

Multiply By To obtain 

meter (m) 3.281 × 100 foot 

centimeter (cm) 3.937 × 10-1 inch 

millimeter (mm) 3.937 × 10-2 inch 

micrometer (μm) 3.937 × 10-5 inch 

square mile (mi

2) 2.590 × 100 square kilometer 

liter (L) 2.642 × 10-1 gallon 

Abbreviated chemical-quality units used in this report: Concentrations of chemical constituents in sediment and fish tissue are given in 

units of milligrams per kilogram (mg/kg), micrograms per kilogram (μg/kg), or nanograms per gram (ng/g). Concentrations of mercury in 

surface water are given in nanograms per liter (ng/L). 

Other abbreviations used in this report: 

CERCLIS Comprehensive Environmental Response Compensation and Liability Information System 

DDD Dichlorodiphenyldichloroethane 

DDE Dichlorodiphenyldichloroethylene 

DDT Total dichlordiphenyltrichloroethane 

IDEM Indiana Department of Environmental Management 

ISQG Canadian Interim Sediment Quality Guidelines 

MIAM Great and Little Miami River Basins 

NAWQA National Water-Quality Assessment 

NPL National Priority List 

NWQL U.S. Geological Survey National Water Quality Laboratory 

NYFFC New York Fish Flesh Criteria 

OEPA Ohio Environmental Protection Agency 

p Binomial probability 

PAH Polycyclic aromatic hydrocarbons 

PCB Total polychlorinated biphenyls 

PEL Probable Effect Level 

rho Spearman correlation coefficient 

RM River mile 

SOC Synthetic organic compound 

SVOC Semivolatile organic compound 

SQG Sediment-quality guideline 

TEL Threshold Effect Level 

TRI Toxic Release Inventory 

USGS U.S. Geological Survey 

Contents VII
Trace Elements and Synthetic Organic Compounds in 

Streambed Sediment and Fish Tissue in the Great and Little 

Miami River Basins, Ohio and Indiana, 1990-98 

By Stephanie D. Janosy 

Abstract 

Streambed-sediment and fish-tissue samples were collected at eight sites in the Great and Little Miami 

Basins as part of the U.S. Geological Survey’s 

National Water Quality Assessment Program. The 

samples were analyzed for trace elements and synthetic organic compounds, including organochlorine 

insecticides, polychlorinated biphenyls (PCBs), and 

semivolatile compounds (SVOCs). Data from stateagency investigations within the study unit (more than 

200 sites) were incorporated to gain a broader perspective of the occurrence and distribution of contaminants 

in the study unit. All data were compared to streambed-sediment-quality guidelines and fish-tissue 

guidelines to identify elevated contaminant concentrations. Guideline exceedances were plotted on distribution maps to identify areas in the study unit that may 

be of potential concern for wildlife health. 

Several trace elements were detected in both 

sediment and fish-tissue samples. In sediment, lead 

and zinc were most frequently detected at levels that 

may have adverse effects on aquatic organisms. Generally, only one of the trace elements analyzed for per 

site exceeded concentrations above which adverse biological effects are frequently anticipated. 

Organochlorine insecticides were infrequently 

detected in sediment or fish tissue throughout the 

study unit. More organochlorine insecticides were 

detected in fish tissues than in sediment; however, 

more guidelines were exceeded in sediment. No distinct geographic overlap between sediment and fishtissue sites was evident with respect to elevated organochlorine insecticide concentrations. Sedimentquality guideline exceedances were generally widespread throughout the study unit, whereas fish-tissue 

guidelines were exceeded only on the Mad River. 

PCBs were detected more often in fish tissue 

than in sediment throughout the study unit. Elevated 

PCB concentrations in fish tissue were common and 

widespread. No distinct geographic overlap of PCB 

exceedances was evident between sediment and fishtissue sites. 

In sediments, elevated concentrations were 

detected most often for SVOCs, particularly for polycyclic aromatic hydrocarbons (PAHs). Areas where 

SVOC guidelines were frequently exceeded include 

the Great Miami River main stem from Dayton to 

south of Hamilton, and the Upper Little Miami River 

Basin in Greene County. 

Overall, a higher frequency of trace-element 

detections in fish tissue and sediment trace-element 

guideline exceedances was found in the Great Miami 

River Basin than in the Little Miami River Basin. 

Organochlorine insecticide guidelines for fish tissue 

and sediment, as well as PCB and SVOC guidelines 

for sediment also were exceeded more frequently in 

the Great Miami River Basin. PCB guideline exceedances for fish tissue were found more often in the Little Miami River Basin. 

Introduction 

In 1991, the U.S. Geological Survey (USGS) began the 

National Water-Quality Assessment (NAWQA) Program. 

Long-term goals of the NAWQA Program are to describe 

the status and trends in the water quality of a large, repreAbstract 1 
sentative part of the Nation’s surface- and ground-water 

resources and to provide a sound scientific understanding of 

the primary natural and human factors affecting the quality 

of these resources (Hirsch and others, 1988). NAWQA 

study-unit investigations, which are long term and cyclic, 

first began in 1991 and were followed by additional study 

unit investigations beginning in 1994 and 1997. The Great 

and Little Miami River Basins is one of more than 50 study 

units originally chosen by the NAWQA Program to represent the diverse geography, water resources, and land and 

water uses in the Nation. The Great and Little Miami River 

Basins study unit (MIAM) includes three large watersheds 

in the Ohio River Basin, largely agricultural watersheds 

affected by two major urban areas and rapid urbanization, 

and a heavily used buried-valley aquifer system that is one 

of the most productive in the Nation (Rowe and Baker, 

1997). 

An integral part of the NAWQA Program is to investigate and evaluate trends of occurrence and distribution of 

targeted contaminants in streambed sediment and fish tissue 

(Shelton and Capel, 1994). Contaminant concentrations in 

sediment and tissue can be several orders of magnitude 

higher than in water and may be detected even when concentrations in the water column are too low for detection 

(Rand, 1995; Crawford and Luoma, 1994). Many of the 

more persistent hydrophobic compounds are removed from 

the water column as they sorb to suspended particles and 

organic material that may become part of the streambed sediment. Contaminants that can accumulate in sediment 

include trace elements, pesticides, and industrial chemicals 

(Lyman and others, 1987). Aquatic organisms are exposed 

to contaminants by direct exposure or by consuming benthic 

biota that have been exposed to the contaminant (Rand, 

1995). Concentrations in fish tissues provide a direct measure of bioavailability and can be used as an indicator of 

potential health risks to fish-eating wildlife (Crawford and 

Louma, 1994). 

To determine contaminant distribution and occurrence across the Nation, the NAWQA Program targets two 

important chemical classes: synthetic organic compounds 

(SOCs) and trace elements. SOCs include organochlorine 

insecticides, polychlorinated biphenyls (PCBs), and other 

semivolatile organic compounds (SVOCs) that were widely 

used from the 1940s to the 1970s and 1980s before many 

were restricted or banned. Many SOCs are toxic and may 

act as carcinogens or endocrine disruptors. Trace elements 

are naturally occurring and can be redistributed in the environment through human activities such as fossil fuel combustion. They may enter aquatic environments through 

point- and nonpoint-source releases and atmospheric deposition. For aquatic biota, trace elements of greatest concern 

are copper, zinc, cadmium, mercury, and lead (Rand, 1995). 

These elements are toxic to organisms above specific 

threshold concentrations, but many of these elements (for 

example, copper and zinc) are necessary for metabolism at 

lower concentrations. Lead, cadmium, and mercury have no 

known biological function. 

Purpose and scope 

This report summarizes streambed sediment and fish-tissue 

data collected by the MIAM personnel during summer 

1998. In addition, data previously collected by state agencies within the study unit are incorporated to gain a better 

perspective of the occurrence and distribution of contaminants. 

Contaminant data are presented and interpreted in 

four ways. First, presence/absence and frequency of contaminant occurrence at MIAM sampling stations are 

described. Second, MIAM contaminant concentrations are 

compared to concentrations found by other NAWQA study 

units throughout the Nation. Third, data from state agencies 

are incorporated to give a regional perspective of occurrence. Fourth, data from all agencies are compared to sediment-quality guidelines and fish-tissue guidelines to 

identify compounds that exceed published limits and, by 

means of occurrence and distribution maps, to identify areas 

that may be a concern for wildlife health. 

For this report, data collected by MIAM NAWQA 

personnel are described as “MIAM data.” “National 

NAWQA data” refers to data collected by other NAWQA 

study units (1991, 1994, or 1997), where available. “Stateagency data” describes data collected by the Ohio Environmental Protection Agency (OEPA) and Indiana Department 

of Environmental Management (IDEM); “study-unit data” 

defines all data collected in the study unit by MIAM, OEPA, 

and IDEM. 

Relations between sediment and tissue concentrations are difficult to determine and were not attempted in 

this report because of the many factors that affect the behavior, fate, and transport of trace elements and synthetic 

organic compounds. Such factors may include chemical 

speciation, water characteristics, physical features such as 

dams, antagonistic effects, and adsorption and desorption 

rates. Fish species, migration, feeding preferences, metabolic rates, and lipid content also must be taken into consideration. 

Description of the Great and Little Miami River Basins 

study unit 

The Great and Little Miami River Basins cover approximately 7,350 mi2

. Three large river systems drain the study 

unit. The Great Miami River (drainage area, 4,124 mi2

) and 

the Little Miami River (drainage area, 1,756 mi2

) are in 

southwestern Ohio, and the Whitewater River (drainage 

area, 1,474 mi

2) is in southeastern Indiana (fig.1). The 

Whitewater River exits Indiana in Dearborn County and 

joins the Great Miami River in Hamilton County near Cin2 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
cinnati. Both the Great and Little Miami Rivers drain 

directly into the Ohio River. Major tributaries in the study 

unit include the Mad and Stillwater Rivers in the Great 

Miami River Basin, East Fork Little Miami River in the Little Miami River Basin, and East and West Fork Whitewater 

Rivers in the Whitewater River Basin. Streamflow in the 

study unit is affected by five flood-retention dams and eight 

lowhead dams in the Great Miami River Basin, one dam on 

the East Fork Whitewater River, and four dams on both the 

East Fork Little Miami River and main stem of the Little 

Miami River (Harrington, 1999). 

The study unit spans two ecoregions, the Eastern 

Corn Belt Plains and the Interior Plateau (Debrewer and 

others, 2000). Approximately 79 percent of land is used for 

agricultural activities, primarily row-crop production of 

corn, soybeans, and wheat. Principal livestock raised are 

swine, cattle, and poultry. Residential, commercial, and 

industrial land uses make up 13 percent of the area, whereas 

the remaining area consists of forests (7 percent) and water 

bodies or wetlands (1 percent). Major industries, which are 

concentrated along the Dayton-Cincinnati corridor, produce 

automobile parts, business and computer equipment, chemicals, household goods, paper products, and processed foods 

and beverages. 

In 1995, the estimated population of the study unit 

was approximately 2.8 million, mostly concentrated near 

the largest cities: Cincinnati, Dayton, and Hamilton, Ohio 

(Rowe and Baker, 1997). A complete description of the 

environmental setting for the study unit can be found in 

Debrewer and others (2000). 

Acknowledgments 

Special thanks are extended to James Stahl (IDEM) for his 

compilation of data and to Dennis Mishne (OEPA) for compilation of data and review of the report. The author thanks 

USGS personnel Ralph Haefner, Daniel Button, Gary 

Rowe, Robin Brightbill, and Dorene MacCoy for their critical reviews of the report. The author also acknowledges Lee 

Hwang of the USGS for his assistance with data and map 

preparation. 

Study design and methods 

Streambed-sediment and fish-tissue samples represented in 

the MIAM data sets were collected during the summer at 

base flow. Samples were collected from eight established 

MIAM sites representing five agricultural, one urban, and 

two mixed-land-use settings. Mixed-land-use settings, hereafter referred to as mixed settings, are defined as sites 

located downstream from drainage basins that are large and 

complex and often contain multiple environmental settings. 

(Shelton, 1994). A summary of sampling sites is listed in 

table 1. Each tissue sample consisted of four to eight liver 

composites for trace-element analyses and four to eight 

whole-fish composites for organic analyses. To allow for 

comparisons between MIAM and other NAWQA study 

units, the common carp (Cyprinus carpio) was selected as 

the target species because of its national abundance and relative ease to collect. A composite of streambed-sediment 

samples was collected from several depositional zones 

within the reach sampling boundaries of approximately 

100 m in length, and then divided into two samples for further processing for trace-element and synthetic-organiccompound analyses. 

Fish tissue was analyzed for 22 trace elements and 28 

organic compounds (organochlorine insecticides, industrial 

compounds, and a chlorinated herbicide); sediments were 

analyzed for 46 trace elements, 33 organochlorine insecticides plus polychlorinated biphenyls (PCBs), and 65 industrial organic compounds. A complete list of chemicals 

analyzed by NAWQA is given in table 2. 

Sampling procedures 

The sampling procedures used for sampling streambed sediment and tissue are briefly described below. A more detailed 

description of sampling procedures for streambed sediment 

can be found in Shelton and Capel (1994). Laboratory procedures used to analyze organic compounds and semivolatile organic compounds in streambed sediment are described 

in Forman and others (1995) and Furlong and others (1996), 

respectively. Protocols used for collecting and processing 

fish tissue for the analysis of trace elements and synthetic 

organic compounds are described in detail in Crawford and 

Luoma (1994). Sediment and tissue data are published in 

Shindel and others (1999) and U.S. Geological Survey 

(2002). 

Sediment. Fine-grained sediment samples were collected from 5 to 10 depositional zones within the sampling 

reach. Sediment was collected at 5 to 10 locations within 

each depositional zone. A total volume of 1.5 L of wet sediment was collected from the top layer (1 cm) of the sediment surface using a Teflon spatula. To control crosscontamination between trace-element and organic samples, 

field personnel wore latex gloves and used separate sampling equipment for each type of sample. Sediments collected for trace-element analysis were processed through a 

63-μm mesh nylon sieve held in a plastic frame over a plastic bottle. Samples collected for analysis of organic compounds were processed through a 2.0-mm stainless steel 

sieve over a baked amber glass jar. Samples were shipped 

on ice to the U.S. Geological Survey National Water Quality 

Laboratory (NWQL) for analysis. 

Fish tissue. Common carp were collected with towed 

electrofishing gear at all locations with the exception of the 

Great Miami River at Hamilton, a nonwadeable site, which 

Study design and methods 3 
4 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins

required the use of an electrofishing boat. Weight, length, and sex were determined for each fish. For trace-element

Figure 1. The Great and Little Miami River Basins study unit, Ohio and Indiana.

EXPLANATION

Troy

Cincinnati

Hamilton

Dayton

LAND USE

 Urban

 Agricultural

 Forest

SAMPLING SITE

0 10 0 0

MILES

KILOMETERS

0 0 20 30

DARKE

RANDOLPH

WAYNE

FAYETTE

FRANKLIN

UNION

PREBLE

MONTGOMERY

BUTLER

HAMILTON

WARREN

CLERMONT BROWN

MIAMI

SHELBY

LOGAN

CHAMPAIGN

CLARK

GREENE

CLINTON

Base from U.S. Geological Survey

digital data 1:100,000, 1983

Albers Equal Area projection

Standard Parallels 29o30' and 45o30',

central meridian -86o

2 3

1
Table 1. Description of sampling sites in the Great and Little Miami River Basins study unit, Ohio and Indiana 

[Major land use percentages were calculated from National Land Cover Data (1992); mi2, square miles] 

Figure 1 Major land use (percent) 

locationn Station number Station name Drainage 

umber 

Latitude Longitude area (mi2) Urban Agricult Forest Other ure 

1 393944084120700 Holes Creek at 

Kettering, Ohio 

2 393259085101200 Whitewater River near 

Nulltown, Ind. 

3 395433084175300 Stillwater River on Old 

Springfield Rd near 

Union, Ohio 

4 395534084091400 Great Miami River near 

Tipp City, Ohio 

5 395650083504400 Mad River near Hwy 41 

near Springfield, 

Ohio 

6 03246400 East Fork Little Miami 

River near 

Williamsburg, Ohio 

7 03245500 Little Miami River at 

Milford, Ohio 

8 392246084340100 Great Miami River 

below Hamilton, 

Ohio 

Urban site 

39°39′44′′ 84°12′07′′ 20 61.9 28.5 9.0 0.6 

Agricultural sites 

39°32′59′′ 85°10′12′′ 533 1.9 88.0 9.1 1.0 

39°54′33′′ 84°17′53′′ 643 2.1 91.6 5.8 0.5 

39°55′34′′ 84°09′14′′ 1,128 3.3 86.7 8.6 1.4 

39°56′50′′ 84°50′44′′ 319 3.1 81.8 14.6 0.5 

39°03′32′′ 84°03′05′′ 234 1.3 85.9 12.2 0.6 

Mixed-land-use sites 

39°10′11′′ 84°17′52′′ 1,202 9.2 73.2 16.5 1.1 

39°22′46′′ 84°34′01′′ 3,636 7.7 80.9 10.4 1.0 

analysis, four to eight livers were removed with Tefloncoated stainless steel forceps, weighed, and composited in a 

glass jar. To avoid sample contamination, field personnel 

wore vinyl gloves and used separate sampling equipment 

for external and internal incisions. For synthetic organic 

compound samples, four to eight whole fish were tagged 

and individually wrapped in aluminum foil. All samples 

were sealed in plastic bags and shipped on dry ice to the 

NWQL for analysis. Analytical methods for tissue are published in Hoffman (1996) and Leiker and others (1995). 

Data analysis 

To better define regional occurrence and distribution of contaminants, post-1990 data collected in the study unit by state 

agencies were combined with the MIAM data for analyses 

(table 3). Sediment and tissue data were compiled from 

reports and electronic data files supplied by OEPA and 

IDEM (D. Mishne, Ohio Environmental Protection Agency, 

written commun., 2001; and J. Stahl, Indiana Department of 

Environmental Management, written commun., 2001). This 

aggregation of streambed-sediment and fish-tissue data 

from multiple sources was complicated by several factors, 

including (1) differences in field methods, (2) variations in 

analytical reporting limits for individual chemicals and over 

time, and (3) variations in target species and (or) target 

organs used for tissue analyses. For example, sediment samples collected by the USGS were sieved in the field to obtain 

the fine-grained fraction of sediment, which generally contains higher concentrations of adsorbed chemicals than 

coarse fractions do. Therefore, USGS analyses may report 

higher concentrations of some contaminants in relation to 

OEPA and IDEM data, which are based on analyses of 

unsieved samples. Laboratory methods at all agencies varied and were continuously being revised and improved, 

yielding multiple detection limits among agencies and, in 

some cases, for individual chemicals. State-agency field and 

laboratory methods are published in agency manuals (Indiana Department of Environmental Management, 1992 and 

1999; Ohio Environmental Protection Agency, 1989, 1995, 

1996 and 1997b). 

Variations in tissue types (fillet, whole fish, or liver) 

or species collected varied among the agencies and was 

dependent on the objective of the individual monitoring program. For example, most studies monitoring contaminant 

concentration in fish tissue focus on possible risks to human 

health and therefore analyze fillets, the edible portion of the 

fish, from sportfish species such as smallmouth bass. 

Study design and methods 5 
Table 2. Constituents analyzed for in streambed sediment and fish tissue by the National Water-Quality Assessment Program 

[*, constituents analyzed for in tissue; **, tissue only; Modified from Shelton and Capel, 1994. Compounds in bold are Priority Toxic Pollutants (U.S. 

Environmental Protection Agency, 1999); •, Chromium III and VI only; ∇, Chlordane; ◊, alpha-Endosulfan and beta-Endosulfan]. 

Major and trace elements 

Aluminum* Cerium Lead* Potassium Tin 

Antimony* Chromium*• Lithium Scandium Titanium 

(Stibium) Cobalt* Magnesium Selenium* Uranium* 

Arsenic* Copper* Manganese* Silver* Vanadium* 

Barium* Europium Mercury* Sodium Yttrium 

Beryllium* Gallium Molybdenum* Strontium* Ytterbium 

Bismuth Gold Neodymium Sulfur Zinc* 

Boron** Iron* Nickel* Tantalum 

Cadmium* Holmium Niobium Thallium 

Calcium Lanthanum Phosphorus Thorium 

Organochlorine insecticides and polychlorinated biphenyls 

Aldrin* Endrin* 

cis-Chlordane* Heptachlor* 

trans-Chlordane* Heptachlor epoxide* 

Chloroneb Hexachlorobenzene* 

Dacthal* alpha-HCH* 

o,p'-DDD* beta-HCH* 

p,p'-DDD* delta-HCH** 

o,p'-DDE* gamma-HCH 

p,p'-DDE* (Lindane)* 

o,p'-DDT* Isodrin 

p,p'-DDT* o,p'-Methoxychlor * 

Dieldrin* p,p'-Methoxychlor * 

Endosulfan I ◊ Mirex* 

cis-Nonachlor*∇

trans-Nonachlor*∇

Oxychlordane*∇

Polychlorinated 

biphenyls 

(PCBs-total)* 

cis-Permethrin 

trans-Permethrin 

Pentachloroanisole* 

Toxaphene* 

Other semivolatile organic compounds 

Acenaphthene p-Cresol Indeno[1,2,3-cd] pyrene 

Acenaphthylene Chrysene Isophorone 

Acridine 4H-cyclopenta[d,e,f]phenanthrene Isoquinoline 

C8-Alkylphenols Dibenz[a,h]anthracene 2-Methylanthracene 

Anthracene Dibenzothiophene 1-Methyl-9H-fluorene 

Anthraquinone 1,2-Dichlorobenzene 1-Methylphenanthrene 

Azobenzene 1,3-Dichlorobenzene 1-Methylpyrene 

Benz[a]anthracene 1,4-Dichlorobenzene Naphthalene 

Benzo[c]cinnoline Diethyl phthalate Nitrobenzene 

Benzo[b]fluoranthene 1,2-Dimethylnaphthalene 4-Nitrophenol 

Benzo[k]fluoranthene 1,6-Dimethylnaphthalene N-Nitrosodiphenylamine 

Benzo[g,h,i]perylene 2,6-Dimethylnaphthalene N-Nitroso-di-n-propyl amine 

Benzo[a]pyrene 3,5-Dimethylphenol Phenanthrene 

2,2'-Biquinoline Dimethyl phthalate Pyrene 

4-Bromophenylphenylether Di-n-butyl phthalate Pentachloroanisole 

Butylbenzyl phthalate 2,4-Dinitrotoluene Pentachloronitrobenzene 

Carbazole 2,6-Dinitrotoluene Phenanthridine 

bis(2-Chloroethoxy) methane Di-n-octyl phthalate Phenol 

4-Chloro-3-methylphenol bis(2-Ethylhexyl) phthalate Quinoline 

2-Chlorophenol 2-Ethylnaphthalene 1,2,4-Trichlorobenzene 

2-Chloronaphthalene Fluoranthene 2,3,6-Trimethylnaphthalene 

4-Chlorophenylphenylether Fluorene 

6 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
-- -- --

Table 3. Maximum number of streambed-sediment and fish-tissue sites per agency incorporated for analyses 

[Number of samples vary per constituent. PCBs, polychlorinated biphenyls; SVOCs, semivolatile organic compounds; --, no whole-body samples] 

Number of sediment sites Number of fish-tissue sites 

Data source Trace Organochlorine PCBs SVOCs Trace Organochlorine PCBs elements insecticides elements insecticides 

U.S. Geological Survey 

MIAM NAWQA 8 8 8 8 8 8 8 

State Agency 

Ohio Environmental 227 176 179 142 33 36 36 

Protection Agency 

Indiana Department of 

Environmental 

Management 

4 8 8 5 

Whole-fish samples were typically used when the objective 

of a program was to assess the health risk to fish-eating 

wildlife; such programs commonly target species such as 

the common carp or a sucker species. NAWQA Program 

objectives are to determine contaminant concentrations that 

may pose a risk to wildlife health; consequently, whole fish 

were used in organic analyses. For trace-element analyses, 

however, whole-fish and fillet samples may be insensitive 

monitors of trace-element concentrations (with the exception of mercury). Polar substances such as cadmium, lead, 

and zinc do not readily bioaccumulate in fish muscle (fillets), where less polar elements tend to accumulate. Instead, 

these elements concentrate in various organs, particularly 

the liver, which commonly has higher metal concentrations 

than other organs and is therefore a good indicator of metal 

concentrations (Crawford and Louma, 1994). To eliminate 

variability in contaminant concentration among tissue types 

sampled and among species because of migration, feeding, 

or metabolism rates, only whole-carp and liver data are 

included in this report. 

Samples with concentrations less than the reporting 

limit were treated as nondetections, and concentrations 

(including estimated concentrations) equal to or above the 

reporting limit were considered detections. All concentrations in fish tissue were reported from the laboratory in wet 

weights, with the exception of NAWQA trace-element data, 

which were converted from dry to wet weights (μg/g) to 

simplify data comparisons. All sediment concentrations 

were reported in dry weights (mg/kg). In this report, total 

dichlorodiphenyltrichloroethane (DDT) consists of the sum 

of concentrations of o,p'-DDT, p,p'-DDT, o,p'-DDD, p,p'-

DDD, o,p'-DDE, and p,p'-DDE. Total chlordane is defined 

as the sum of concentrations of cis-chlordane, transchlordane, cis-nonachlor, trans-nonachlor, and 

oxychlordane. Polychlorinated biphenyls consist of 209 

synthetic chlorinated aromatic hydrocarbons. Total PCB 

concentration, as reported by the NWQL, is the sum of three 

common industrial mixes found in the United States: Aroclors 1242, 1254, and 1260 (Dennis J. Markovchick, 

National Water Quality Laboratory, written commun., 

2001). For consistency, OEPA and IDEM data for these 

three types of Aroclors were summed and reported as total 

PCBs. 

MIAM, national NAWQA, and IDEM samples were 

collected at one point in time at a single location. OEPA 

samples were also collected from a single location but at 

some locations samples may have been collected twice during 1990–98. Only the most recent sample collected was 

considered for analyses. For state-agency data, the number 

of samples may vary per compound analyzed. 

Standards and guidelines 

Contaminant concentrations measured in sediment and tissue discussed in this report were compared to sedimentquality guidelines and fish-tissue guidelines to identify 

areas and contaminants of concern with respect to their 

potential harmful effects on the aquatic biota. Guidelines 

are important tools for maintaining sediment quality, protecting benthic organisms, and identifying areas in need of 

restoration (Canadian Council of Ministers of the Environment, 1999). There are currently no sediment-quality criteria for the protection of benthic organisms in the United 

States; therefore, NAWQA-recommended Canadian guidelines were used for comparisons (U.S. Geological Survey, 

2001) (table 4). The Canadian Interim Sediment Quality 

Guidelines (ISQG) were used to evaluate the sediment quality for SOCs and trace elements (Canadian Council of Ministers of the Environment, 1999). These guidelines consist 

Study design and methods 7 
--

--

--

--

--

--

--

Table 4. Canadian Sediment Quality Guidelines and New York Fish Flesh Criteria for trace elements, organochlorine insecticides, total 

polychlorinated biphenyls, and semivolatile organic compounds including common sources, uses, and examples of potential adverse 

effects to wildlife 

[--, not available; PEL, Probable Effect Level; TEL, Threshold Effect Level; ug/g, micrograms per gram; μg/kg,micrograms per kilogram ] 

Canadian Sediment 

Trace element or Quality Guidelines New York Fish Common sources or uses Examples of potential 

organic compound Flesh Criteria adverse effects to fish 

TEL PEL 

Trace elements (μg/g) 

Arsenic 5.9 17.0 Orchard and forest sprays, wood preservative, 

herbicides, pesticides, glass and textile 

manufacuring, animal-feed additives (Rheaume 

and others, 2000; Agency for Toxic Substances 

and Disease Registry, 2001c). 

Cadmium 0.6 3.5 Batteries, plastics, sludge disposal, metal coatings 

(Rheaume and others, 2000; Agency for Toxic 

Substances and Disease Registry, 2001b). 

Chromium 37.3 90.0 Chrome plating, leather tanning, wood preserving, 

photocopying machines, steel and glass 

manufacturing (Agency for Toxic Substances and 

Disease Registry, 2001b; U.S. Department of 

Energy, 2002). 

Copper 35.7 197.0 Plumbing; fungicides and algal control; production 

of wire, metal, pipes and pennies; treatment for 

plant diseases; water treatment; wood, leather and 

fabric preservative (Rheaume and others, 2000; 

Agency for Toxic Substances and Disease 

Registry, 2001b). 

Lead 35.0 91.3 Batteries, radiation protection for televisions and 

computers, circuit boards in computers and other 

electronic equipment, optical and nuclear medical 

technology, steel and glass manufacturing 

(Rheaume and others, 2000; Agency for Toxic 

Substances and Disease Registry, 2001b; U.S. 

Department of Energy, 2002). 

Mercury 0.17 0.486 Batteries, paint, coal and waste combustion, 

thermometers, dental fillings, steel and glass 

manufacturing (Rheaume and others, 2000; 

Agency for Toxic Substances and Disease 

Registry, 2001b; U.S. Department of Energy, 

2002). 

Zinc 123 315 Production of alloys and brass in steel and iron 

products, road-surface runoff, agricultural 

erosion, domestic and trial sewage, printing 

plates, dye manufacture, cosmetics, 

pharmaceuticals, pesticides, fertilizers (Rheaume 

and others, 2000). 

Increased production of 

mucus causing suffocation, 

damage to gill epithelium 

(Irwin and others, 1997). 

Behavioral, growth, and 

physiological problems 

(Irwin and others, 1997). 

Decreased weight gain, 

impaired reproduction 

(Irwin and others, 1997). 

Altered migratory and other 

behaviors; fathead minnow 

embryos hatch at earlier 

stages of development 

(Irwin and others, 1997). 

Formation of excess mucus 

that can coat the gills and 

cause respiratory problems 

(Irwin and others, 1997). 

Reduced reproductive 

success, impaired growth, 

and developmental and 

behavioral abnormalities 

(Eisler, 1985-99). 

Destruction of gill 

epithelium and consequent 

tissue hypoxia (Eisler, 

1985-99). 

Synthetic organic compounds 

Organochlorine insecticides and polychlorinated biphenyls (PCBs) (μg/kg) 

Total chlordane 4.5 8.87 500 Pesticide for homes, lawns, gardens, turf, corn, Endrocrine distruption, liver 

potatoes, and tomatoes (Agency for Toxic and kidney lesions, 

Substances and Disease Registry, 1994). increased respiration rate, 

abnormal swimming 

patterns, convulsions, and 

loss of equilibrium 

(Nowell and others, 1999; 

Eisler, 1985-99). 

8 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
--

--

-- --

-- -- --

-- --

-- --

-- --

Table 4. Canadian Sediment Quality Guidelines and New York Fish Flesh Criteria for trace elements, organochlorine insecticides, total 

polychlorinated biphenyls, and semivolatile organic compounds including common sources, uses, and examples of potential adverse 

effects to wildlife—Continued 

[--, not available; PEL, Probable Effect Level; TEL, Threshold Effect Level; ug/g, micrograms per gram; μg/kg,micrograms per kilogram ] 

Canadian Sediment 

Trace element or Quality Guidelines New York Fish Common sources or uses Examples of potential 

organic compound Flesh Criteria adverse effects to fish 

TEL PEL 

DDD 3.54 8.51 

DDE 1.42 6.75 

DDT 1.19 4.77 200 (total DDT) 

Dieldrin 2.85 6.67 120 

Endrin 2.67 62.4 25 

gamma-HCH 0.94 1.38 100 (total HCH) 

Heptachlor epoxide 0.60 2.74 200 

(total heptachlor) 

Hexachlorobenzene 330 

Mirex 330 

Total PCBs 34.1 277 110 

Metabolite of DDT. 

Metabolite of DDT. 

Insecticide (Rheaume and others, 2000). 

Insecticide primarily for corn and citrus, sheep dips, 

treatment of wood, mothproofing woolen goods, 

public health control of mosquitoes and tsetse 

flies (Department of Health and Human Services, 

2002; Larson and others, 1999; Agency for Toxic 

Substances and Disease Registry, 1993). 

Insecticide on field crops such as cotton and grains, 

control of rodents and birds (Environmental 

Media Services, 2002). 

Treatment of wood-inhabiting beetles and seeds, 

flea and lice dip, soil treatment; used in lotions, 

creams, and shampoos for the control of lice and 

mites in humans (U.S. environmental Protection 

Agency, 2002c). 

Fire ant control in power transformers. 

Used in manufacture of chemicals used as solvents, 

other chlorine-containing compounds, and 

pesticides, in combustion processes such as 

burning of city wastes, produced as a byproduct 

in waste streams of chlor-alkali and wood 

preserving plants (Agency for Toxic Substance 

and Disease Registry, 1997). 

Control of fire ants, flame retardant in plastics, 

rubber, paint, paper, and electrical goods (Agency 

for Toxic Substance and Disease Registry, 1996). 

Used in adhesives, inks, carbonless duplicating 

paper, and as coolants for capacitors and 

transformers (Eisler, 1985-99; Agency for Toxic 

Substance and Disease Registry, 2001a; U.S. 

Environmental Protection Agency, 2001). 

Endrocrine disruption, liver 

and kidney lesions 

(Nowell and others, 1999). 

Endrocrine disruption, liver 

and kidney lesions 

(Nowell and others, 1999). 

Endrocrine disruption, liver 

and kidney lesions 

(Nowell and others, 1999). 

Endrocrine disruption, liver 

and kidney lesions 

(Nowell and others, 1999). 

Highly toxic to fish. 

(Environmental Media 

Services, 2002). 

Highly to very highly toxic 

(Extoxnet, 2001). 

Very highly toxic to most 

fish species (Extoxnet, 

2001). 

Slightly toxic (Extoxnet, 

2001). 

Known endocrine disruptors, 

reproductive failure, birth 

defects, skin lesions, 

tumors, and liver disorders 

(Eisler, 1985-99). 

Semivolatile organic compounds (SVOCs) (μg/kg) 

Acenaphthene 6.71 88.9 Used in dyes, plastics, insecticides and fungicides 

(Irwin and others, 1997). 

Acenaphthylene 5.87 128 Coal and tar products, product of combustion 

(Irwin and others, 1997). 

Anthracene 46.9 245 Exhaust from motor vehicles; cigarette, marijuana 

and cigar smoke; emissions from coal-, oil-, and 

wood-burning stoves, furnaces, and power plants 

(Irwin and others, 1997). 

Study design and methods 9 
Table 4. Canadian Sediment Quality Guidelines and New York Fish Flesh Criteria for trace elements, organochlorine insecticides, total 

polychlorinated biphenyls, and semivolatile organic compounds including common sources, uses, and examples of potential adverse 

effects to wildlife—Continued 

[--, not available; PEL, Probable Effect Level; TEL, Threshold Effect Level; ug/g, micrograms per gram; μg/kg,micrograms per kilogram ] 

Canadian Sediment 

Trace element or Quality Guidelines New York Fish Common sources or uses Examples of potential 

organic compound Flesh Criteria adverse effects to fish 

TEL PEL 

Benz[a]anthracene 31.7 385 -- Engine exhaust, cigarette smoke, coal-tar pitch, --

coke oven emissions (Irwin and others, 1997). 

Benzo[a]pyrene 31.9 782 -- Crude oils and coal tars; used in furnace blacks, --

automobile tires, and rubber stoppers (Irwin and 

others, 1997). 

Chrysene 57.1 862 -- Coal tar, exhaust from motor vehicles and other --

gasoline and diesel engines, emission from coal-, 

oil-, and wood-burning stoves and furnaces, 

cigarette smoke (Irwin and others, 1997). 

Dibenz[a,h]anthracene 6.22 135 -- Product of incomplete combustion, forest fires --

(Irwin and others, 1997). 

Fluoranthene 111 2355 -- Exhaust from gasoline engines, coal tar, coke ovens, A co-carcinogen (a chemical 

crude oil (Irwin and others, 1997). that is noncarcinogenic, 

"but when present with 

another carcinogen, will 

enhance that chemical's 

carcinogenicity") (Irwin 

and others, 1997). 

9H Fluorene 21.2 144 -- Product of incomplete combustion, cigarette smoke, --

exhaust from gasoline engines (Irwin and others, 

1997). 

2-Methylnaphthalene 20.2 201 -- -- --

Naphthalene 34.6 391 -- Used in petroleum products and byproducts, jet --

fuels (Irwin and others, 1997). 

Phenanthrene 41.9 515 -- Product of incomplete combustion of fossil fuels --

and wood, auto emissions, steel manufacturing, 

and foundries (U.S. Department of Energy, 

2002). 

Pyrene 53.0 875 -- Product of incomplete combustion, exhaust from --

gasoline and diesel engines (Irwin and others, 

1997). 

Diethylphthalate -- -- -- Commonly used as a plasticizer, in insecticide --

sprays, and the manufacture of perfume 

compounds and varnishes (National Institute of 

Health Sciences, 2002). 

2,6-Dinitrotoluene -- -- -- Commonly used in the manufacturing of --

polyurethane, as a component of explosives and 

automobile airbags, and in dye processes (U.S. 

Department of Energy, 2002; Agency for Toxic 

Substances and Disease Registry, 2001b). 

p-Cresol Automobile emissions, metal refining, and --

manufacturing of chemicals and wood pulp (U.S. 

Environmental Protection Agency, 2002c). 

10 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
of two effect values, the threshold effect level (TEL; also 

known as sediment-quality guideline, SQG), and the probable effect level (PEL). The TEL defines the concentration 

below which adverse effects are rarely anticipated, whereas 

the PEL defines the concentration above which adverse 

effects are frequently anticipated (Canadian Council of 

Ministers of the Environment, 1999). NAWQA trace-element samples were based on analyses of the sieved <63-μm 

sediment fraction, where concentrations tend to be highest; 

therefore, comparisons with the Canadian guidelines, which 

were based on analyses of unsieved- sample data, may overestimate the effects of trace-element concentrations in sediments (Deacon and Stephens, 1998). 

Generally, standards or guidelines for contaminant 

concentrations in fish tissue apply to edible portions of fish 

that are most likely to be consumed by humans. There are 

currently no published guidelines, standards, or aquatic criteria for trace-element concentrations in fish liver. Wholefish samples submitted for organic analyses were compared 

to New York Fish Flesh Criteria (NYFFC; Newell and others, 1987) for the protection of fish-eating wildlife. 

TRACE ELEMENTS 

Sediment and fish-tissue quality 

Although direct comparisons of streambed sediment and 

fish-tissue data could not be made among the agencies, 

aggregation of state-agency data with MIAM data does 

allow for the display of areas of guideline exceedances 

within the study unit. Geographic distributions of sediment 

and tissue sites showing concentrations in exceedance of 

guidelines and (or) number of detections of trace elements 

in fish tissue are used to identify areas where wildlife health 

is of potential concern and where further investigations may 

be warranted. Currently, no health standards or aquatic criteria have been developed for trace elements in fish livers; 

therefore, the number of trace elements detected per sample 

location is shown. Only constituents with current guidelines 

are shown. Concentrations of other constituents may be 

atlevels that could have adverse biological effects, but 

guidelines have not yet been established. Percentages of 

sites where SOC and trace elements were detected are 

shown in figure 2. 

SYNTHETIC ORGANIC COMPOUNDS 

PERCENTAGE OF SITES 

WITH DECTECTIONS 

120 

100 

80 

60 

40 

20 

0 

20 

40 

60 

80 

100 

120 

16 

38 

8 

8 

41 

41 

8 

16 8 

242 233 

233 

230 

239 

136 

222 186 

221 

45 0 

30 30 

45 

45 

45 

45 

37 0 

45 

38 37 40 

30 

44 

0 

103 

10616 

63 

70 71101 

103 

102 

109 

102 

102102 94 

49 

195 

96 Fish tissue 

Streambed-sediment 

45 Number of sites

ARSENIC 

CADMIUM 

CHROMIUM 

COPPER 

LEAD 

MERCURY 

NICKEL 

SELENIUM 

ZINC 

ALDRIN 

BENZO[

A]PYRENE 

cis-CHLORDANE 

trans-CHLORDANE 

DDD DDE 

DDT 

DIELDRIN 

ENDOSULFAN 1 

FLUORANTHENE 

HEPTACHLOR EPOXIDE 

HEXACHLOROBENZENE 

METHOXYCHLOR 

MIREX 

OXYCHLORDANE 

TOTAL PCB'S 

PYRENE 

Figure 2. Percentage of sites where trace elements and synthetic organic compounds were detected within the Great and Little Miami 

River Basins, Ohio and Indiana, 1990–1998. (Fish-tissue data include U.S. Geological Survey, Ohio Environmental Protection Agency, and 

Indiana Department of Environmental Management sites.) 

Sediment and fish-tissue quality 11 
For each chemical group (trace elements, organochlorine insecticides, PCBs, and SVOCs) the occurrence 

and distribution in each media (streambed sediment and fish 

tissue) are discussed. A brief discussion of chemical uses 

and concerns is also presented. For each media type, results 

are described for MIAM sampling locations, national 

NAWQA data (when available), state-agency data, and 

constituents most frequently found. Samples for all data 

sets were predominantly from agricultural areas; therefore, 

an even distribution of sampling locations was not available, 

and the influence of land use on contaminant concentrations 

could not be accurately determined. 

Trace elements 

MIAM sediment and tissue samples were analyzed 

for 46 and 22 trace elements, respectively. Selected trace 

elements that have been classified by the U.S. Environmental Protection Agency (1999) as “priority pollutants” and are 

considered to be toxic to aquatic organisms—arsenic, cadmium, chromium, copper, lead, mercury, nickel, selenium, 

and zinc—are the focus of this paper. 

Streambed sediment. Trace-element concentrations 

in sediments generally increase with decreasing sediment 

particle size (Shelton and Capel, 1994). Median sand, silt, 

and clay percentages among the MIAM sites were 93.1, 4.1, 

and 3.1, respectively. Particle-size distribution and organiccarbon concentrations at MIAM sampling sites are listed in 

table 5. State-agency particle-size distribution is discussed 

where data were available; however, organic-carbon data 

were not available for state-agency samples. 

All nine trace elements of interest were detected at 

each MIAM sampling location. Cadmium, copper, and mercury concentrations were highest at the mixed-land-use site 

Great Miami River below Hamilton. Sediment samples 

from the urban site, Holes Creek, had the greatest concentrations of arsenic, nickel, and chromium. The second highest concentrations of zinc, arsenic, copper, nickel, and 

cadmium were detected at the agricultural site Great Miami 

River at Tipp City. The percentages of silt and clay at these 

sites were higher than the median percentages for the overall MIAM data set (table 5), so the higher proportion of 

fineparticles may contribute to the higher concentrations of 

trace elements at these sites. No PELs were exceeded; however, TELs were exceeded for arsenic and chromium 

Table 5. Particle-size distribution and organic-carbon concentrations at MIAM streambed-sediment sampling 

sites, Ohio and Indiana, 1998 

[mm, millimeters; μm, micrometers] 

Percentage in streambed sediment 

Organic 

Station name Sand 

(<2 mm and 

>0.062 mm) 

Silt 

(<0.062 mm 

and 

>0.004 mm) 

Clay 

(<0.004 mm) 

carbon, 

(<63 μm dry 

weight, 

percent) 

Holes Creek at Kettering, Ohio 88.8 5.0 6.2 1.11 

Whitewater River near Nulltown, Indiana 94.7 3.8 1.5 1.79 

Stillwater River on Old Springfield Rd near 95.8 1.6 2.6 2.62 

Union, Ohio 

Great Miami River near Tipp City, Ohio 91.5 4.4 4.1 2.38 

Mad River near Hwy 41 near Springfield, Ohio 82.4 11.3 6.3 2.14 

East Fork Little Miami River near 98.5 0.9 0.6 1.49 

Williamsburg, Ohio 

Little Miami River at Milford, Ohio 97.2 1.6 1.2 2.20 

Great Miami River below Hamilton, Ohio 90.7 5.7 3.6 2.32 

Median 93.1 4.1 3.1 2.2 

Mean 92.5 4.3 3.3 2.0 

12 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
15 

r = 0.707 

p = 0.049 

sites (fig. 5). Zinc and lead concentrations exceeded PELs 

ARSENIC CONCENTRATION,

most often. Zinc was detected at all 213 state-agency sites. 

IN MICROGRAMS PER GRAM14 Concentrations exceeded PELs at 16 sites (7.5 percent), 5 of 

which were on Dicks Creek downstream from Middle- 13 town. Of the 231 state-agency sites analyzed for lead, con12 centrations were detected at 151 sites (65 percent), and 15 

concentrations (6.5 percent) exceeded the PEL. Lead was 

11 the only trace element to exceed a PEL in the Whitewater 

10 River Basin; it was detected at 99.3 μg/g at the East Fork 

Whitewater River below Richmond. Arsenic concentrations 

9 exceeded TELs most often. Of 234 state-agency sites, 105 

exceeded TELs (45 percent); 60 exceedances were in the 

8 Great Miami River Basin and 45 in the Little Miami River 

7 Basin, 5 of which were from Turtle Creek, a Little Miami 

0 1 2 3 4 5 6 7 tributary. Particle size was not an important factor influenc- PERCENT CLAY 

(<0.004 MILLIMETER) ing concentrations of lead or zinc in the study unit, but it 

could be affecting arsenic concentrations. No statistically 

significant correlation (Spearman) was found between lead 

Figure 3. Arsenic concentrations as a function of or zinc and particle-size distribution; however, a correlation 

sediment clay content at the Great and Little Miami was found between arsenic concentrations and percentage 

River Basin study unit sampling locations, Ohio and of silt (rho= 0.49, p = <0.0001) and clay (rho = 0.28, p = 

Indiana, 1998. 0.0003). PEL were also exceeded for concentrations of 

arsenic (5 sites), cadmium (5 sites), chromium (3 sites), and 

mercury (1 site). 

concentrations at all MIAM sites and at one or more sites Areas of elevated trace-element concentrations in 

for zinc (five sites), cadmium (two sites), and lead (one the study unit include selected reaches of the Great Miami 

site). Arsenic has a tendency to adsorb to sediments, espe- River tributaries Mad River near Springfield and Dicks 

cially clay particles (Irwin and others, 1997). This was seen Creek, the Upper Great Miami River main stem near Troy, 

at the MIAM sites where increased arsenic was found with and the Little Miami River at river mile (RM) 50.75. Dicks 

increasing clay content (rho=0.707, p=0.049) (fig. 3). Creek had the most trace-element PEL exceedances (five) of 

Concentrations of zinc in sediment were highest at all tributaries. On the main stem, the Great Miami River 

two agricultural sites, East Fork Little Miami River site at (RM) 51.3 had the greatest number of PEL exceed-

(160 μg/g) and Great Miami River at Tipp City (150 μg/g). ances with six (arsenic, cadmium, chromium, lead, mercury, Lead concentrations at MIAM sites were greatest and and zinc) followed by Little Miami at RM 50.75 with three 

exceeded the TEL of 35 μg/g at the two mixed-land-use (arsenic, cadmium, and lead). Of the 32 sites where sedi- sites, Little Miami River (38 μg/g) and Great Miami River at ment exceedances were detected, 21 (66 percent) were in 

Hamilton (36 μg/g). Clay and silt percentages and organic- the Great Miami River Basin and 17 (53 percent) of these 

carbon concentrations at these sites were higher than the were from tributaries. A higher frequency of exceedances 

MIAM medians (table 5) and are potential factors contribut- was found in the Great Miami River Basin (21 of 110 sites, ing to elevated lead concentrations at these sites. 19 percent exceedance) than in the Little Miami River Basin MIAM sediment data were compared with national (11 of 126 sites, 8.7 percent exceedance). NAWQA trace-element data collected as part of studies 

beginning 1991 and 1994 (fig. 4). The national median con- Fish tissue. Arsenic, cadmium, copper, mercury, 

centrations of the trace elements were calculated from the selenium, and zinc were detected in fish tissue samples colresults of Wentz (1999). All MIAM sites exceeded the lected at all MIAM sites. The highest concentrations of copnational NAWQA median for arsenic. Concentrations were per (42.3 μg/g) and zinc (279 μg/g) were in tissue samples 

higher than the median for copper and nickel (6 sites), zinc from the urban site, Holes Creek. Samples from the agricul- 

(5), selenium and mercury (4), lead and cadmium (3), and tural site Stillwater River had the highest concentrations of 

chromium (1). arsenic (0.35 μg/g) and mercury (0.09 μg/g). Cadmium was 

For state-agency data, the most commonly detected highest at the Great Miami River at Hamilton (12.1μg/g) 

elements were zinc, copper, arsenic, cadmium, chromium, and Stillwater River (12.0 μg/g) sites. Lead was detected at 

lead, nickel, selenium, and mercury (100, 99, 96, 94, 78, 65, all MIAM sites with the exception of Mad River. According 

57, 49, and 42 percent of sites, respectively). PEL guide- to Irwin (1997), concentrations of lead in fish tissue tend to 

lines for one or more trace elements were exceeded at 32 increase with increasing fish age. MIAM age data showed 

Trace elements 13 
1 10 

CHROMIUM 

COPPER 

LEAD 

NICKEL 

ZINC 

1 10 100 1,000 10,000 100,000 

ARSENIC 

CADMIUM 

MERCURY 

SELENIUM 

0.01 0.1 1 10 100 1,000 

CONCENTRATION, IN MICROGRAMS PER GRAM 

EXPLANATION 

BED-SEDIMENT-QUALITY GUIDELINES 

Less than Threshold Effect Level (TEL) 

Greater than TEL and less that Probable Effect Level (PEL) 

Greater than PEL 

No guidelines 

SUMMARY STATISTICS 

NAWQA composite range 

NAWQA composite median 

SAMPLING SITE 

Agriculture 

Urban 

Mixed 

Figure 4. Concentrations of selected trace elements at Great and Little Miami River sites compared to Canadian Sediment-Quality Guidelines and selected 1991 and 1994 national NAWQA study units. 

no correlation between fish age and lead concentrations (rho 

= 0.48, p = 0.23). Summaries of national NAWQA data for 

trace elements in tissue were not available. Results of a 

national assessment of mercury contamination at 21 study 

units, including the MIAM, are summarized in Appendix A. 

State-agency data were available for mercury, lead, 

selenium, cadmium, and arsenic. Mercury (at 33 of 33 sites) 

and cadmium (at 27 of 30 sites) were detected most often, 

followed by lead (at 27 of 33 sites). Concentrations of mercury and lead were highest on the main stem Little Miami 

River, RM 83.1 and RM 64.2, (0.274 μg/g and 1.88 μg/g, 

respectively). Six of the seven highest concentrations of 

mercury were found in samples from three sites on the Little 

Miami River main stem between RM 18.5 and 38.6 and at 

three sites on the Stillwater River between RM 12.1 and 

15.4. Cadmium was detected at 27 of 30 state-agency sites 

(90 percent). Lead was detected at 29 of 33 (88 percent) of 

the state-agency sites. The highest concentration of lead 

(1.18 μg/g) was detected at Little Miami River RM 64.2. 

Four of the six highest lead concentrations were detected on 

the Great Miami River main stem; three were in Miami 

County within RM 114 and 95 in the upper Great Miami 

River. Of the samples with trace-element detections, 3 or 

more metals were detected at 27 Great Miami River Basin 

sites (76 percent). Detections of trace elements were most 

frequent on the Mad River near Springfield; on the Great 

Miami River main stem in the vicinity of Middletown, 

Hamilton, and north of Dayton; and along the main stem of 

the Little Miami River. 

Possible sources of trace elements in sediment and 

tissue. Zinc, lead, and arsenic were detected more frequently at elevated concentrations than the other metals of 

interest. Zinc was the most commonly detected trace element in sediment, and more guideline exceedances were 

found for zinc than for any other element. Both urban and 

agricultural land uses are possible contributors of zinc in the 

study unit. Several industries in the area generate zinc 

wastes from plating, polishing, and metal-coating processes. 

14 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
Trace elements 15

Figure 5. Location of streambed-sediment samples exceeding Canadian Sediment-Quality Guideline Probable Effect Levels 

(PELs) and trace-element detections in fish-tissue samples in the Great and Little Miami River Basins, Ohio and Indiana, 

1990–98.

MILES

KILOMETERS

Troy EXPLANATION

LAND USE

Urban

Other

TRACE ELEMENTS

Streambed sediment–

number of PEL

exceedances

1-2

3-4

5-6

none

Fish-tissue–number of

detections at site

1-2

3-4

5-6

7-9
Motor-vehicle part production and steel mills are the most 

common contributors of zinc-containing generated waste in 

the study unit (U.S. Environmental Protection Agency, 

2002b). Industrial land use in Miami County also may contribute to elevated trace-element concentrations in this area. 

According to Toxic Release Inventory (TRI) data, industries 

in Miami County are significant contributors of trace-element waste, particularly zinc and lead, released onsite and 

offsite in the study unit (U.S. Environmental Protection 

Agency, 2002b). PEL exceedances for zinc concentrations 

were found at sites on Dicks Creek, which receives treated 

effluent from steel-manufacturing facilities in Butler 

County (Ohio Environmental Protection Agency, 1997a). 

Zinc was detected at all MIAM fish-tissue sites. Low concentrations of zinc are necessary for fish metabolism (Eisler, 

1985-99). Physical conditions that increase zinc bioavailability (low pH, alkalinity, dissolved oxygen, and high temperatures) (Eisler, 1985-99) are not found in most surface 

waters in the MIAM study unit. 

Lead guidelines for sediment were exceeded more 

often than those for any other element with the exception of 

zinc. Large sources of lead in the study unit are steel mills 

and blast furnaces, motor vehicle part production, and electronics manufacturing (U.S. Environmental Protection 

Agency, 2002b). Elevated concentrations of lead in fish tissue were detected between RM 114 and RM 95 in the Upper 

Great Miami River and are likely related to industrial land 

use in Miami County. Five Comprehensive Environmental 

Response Compensation and Liability Information System1 

(CERCLIS) sites are upstream near the city of Troy; two of 

these, an incinerator and lead-battery reclamation facility, 

are National Priority List (NPL) sites (U.S. Environmental 

Protection Agency, 2002a). Lead may enter surface water 

from atmospheric fallout, runoff, or wastewater. Once in the 

water column, lead adsorbs to organic matter and clay minerals (Irwin and others, 1997). No correlation was found 

between lead concentrations and clay distribution in the 

study unit. Lead, which has no known essential biological 

function, is highly toxic to fish, particularly at early life 

stages (Irwin and others, 1997). Increasing fish age, a possible factor contributing to increased lead concentrations, did 

not correlate with elevated lead concentrations in fish tissue 

at the MIAM sampling sites. 

Arsenic concentrations exceeded more sediment 

TELs than did concentrations of any other trace element in 

the study unit. Arsenic adsorbs from water to sediments, 

especially clays (Irwin and others, 1997). Arsenic concentrations at state-agency sites slightly increased with percent 

clay and silt; therefore, particle-size distribution may be one 

factor affecting arsenic concentrations in the study unit. The 

1 CERCLIS database contains general information on Superfund 

sites in the United States and its territories, including location, 

status, and actions taken. 

majority of arsenic exceedances were in the Great Miami 

River Basin, where streambeds consisting mostly of silt are 

found at 36 percent of the sample sites. Possible point 

sources of arsenic in the study unit are NPL sites including 

an incinerator, landfills, and an industrial-chemical waste 

transfer, disposal, and storage facility. Agricultural land use 

and feedlots, which are common in the study unit, also are 

possible sources; certain arsenicals have been used with 

chickens to increase egg production and with swine to 

increase rate of weight gain and to control dysentery (Irwin 

and others, 1997). 

Synthetic organic compounds 

For the purpose of this report, synthetic organic compounds 

(SOCs) include organochlorine insecticides, polychlorinated biphenyls (PCBs), and other semivolatile organic 

compounds (SVOCs). Each of these organic compounds is 

discussed individually in the following sections. 

Synthetic organic compounds were not normalized 

for carbon content because of the low number of detections, 

and total organic carbon concentrations were not quantified 

for most of the non-USGS data. Spearman correlation coefficients were calculated to determine whether tissue concentrations correlated with lipid content. Analyses for selected 

compounds (dichlorodiphenyldichloroethylene (DDE), 

rho= 0.26 p = 0.15; dieldrin, rho = 0.23, p = 0.30) showed 

no significant correlation; therefore, organochlorine insecticide concentrations were not normalized for lipid content. 

Organochlorine insecticides. MIAM sediment and 

tissue samples were analyzed for 31 and 27 organochlorine 

insecticides, respectively. Sixteen of these compounds are 

listed as Priority Pollutants by the USEPA (1999). Organochlorine insecticides are among the most persistent SOCs 

in the environment because of their low water solubility, 

tendency to sorb to suspended particles and sediments, and 

resistance to biotic degradation and metabolic breakdown 

(Rinella and others, 1999). Organochlorine insecticides may 

enter the aquatic environment from agricultural and urban 

sources through soil erosion, runoff, and precipitation. 

Most organochlorine insecticides are no longer used for 

agriculture in the United States, but they are still manufactured here for use in other countries. 

Streambed Sediment. Few organochlorine insecticides 

were detected in streambed sediments collected at the 

MIAM sites. Of the 31 compounds analyzed, 5 compounds 

were detected: trans-nonachlor, heptachlor epoxide, cischlordane, trans-chlordane, and dieldrin. The highest concentrations of cis-chlordane and trans-chlordane were 

detected at the mixed-land-use site Great Miami River at 

Hamilton. The only insecticide to exceed a guideline was 

heptachlor epoxide; the concentration of 1.1 μg/kg detected 

at the urban site, Holes Creek, exceeded the TEL 

16 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
DIELDRIN 

cis-CHLORDANE 

trans-CHLORDANE 

HEPTACHLOR EPOXIDE 

trans-NONACHLOR 

0.1 1 10 100 

CONCENTRATION, IN MICROGRAMS PER KILOGRAM 

EXPLANATION 

BED-SEDIMENT-QUALITY GUIDELINES 

Less than Threshold Effect Level (TEL) 

Greater than TEL and less than Probable Effect Level (PEL) 

Greater than PEL 

SUMMARY STATISTICS 

NAWQA composite range 

NAWQA composite median 

NAWQA minimum concentration less than the detection limit 

SAMPLING SITE 

Agriculture 

Urban 

Mixed 

Figure 6. Concentrations of selected organochlorine insecticides at MIAM streambed-sediment sites compared to Canadian SedimentQuality Guidelines and data from selected 1991 and 1994 national NAWQA study units. (National medians were below the minimum 

detection limit for all compounds at sites with mixed and agricultural land use. Medians at urban sites are shown where available.) 

of 0.6 μg/kg. Cis-chlordane, trans-chlordane, and transnonachlor also were detected at Holes Creek but at concentrations below the Canadian guidelines. MIAM organochlorine insecticide data were compared to national summary 

statistics computed for organochlorine pesticides in streambed sediment from 1991 and 1994 NAWQA study units 

(fig. 6). Cis- and trans-chlordane concentrations at Holes 

Creek (1.6 μg/kg) were higher than the median of 1.1 μg/kg 

for urban sites. All MIAM agricultural sites exceeded the 

national median for dieldrin (<1 μg/kg). Concentrations at 

the mixed-land-use site Great Miami River at Hamilton 

exceeded the national median for cis- and trans-chlordane 

(<1 μg/kg), heptachlor epoxide (<1 μg/kg), and trans-nonachlor (<1 μg/kg). 

In state-agency data, the most commonly detected 

organochlorine insecticides were dieldrin, cis-chlordane, 

and hexachlorobenzene (35, 33, and 24 percent of all sites, 

respectively). Organochlorine insecticide concentrations 

exceeded PELs at 25 of 184 sites (fig. 7). A higher frequency of PEL exceedances was found in the Great Miami 

River Basin (14 of 68 sites, 21 percent) than in the Little 

Miami River Basin (11 of 116 sites, 9 percent). PELs were 

exceeded for concentrations of dieldrin, total chlordane, lindane, heptachlor epoxide, DDT, and DDE. Concentrations 

of total chlordane exceeded the PEL at seven sites. Elevated 

total chlordane concentrations ranged from 10.9 μg/kg to 

64 μg/kg, the latter being found at the Great Miami River 

RM 0.16. Five of seven sites with elevated concentrations 

were from the Little Miami River Basin, and four of those 

five were from Little Beaver Creek, a tributary southeast of 

Dayton in Greene County. Concentrations of dieldrin 

exceeded PELs most often (12 sites), followed by total chlordane (8 sites), lindane (4 sites) DDT (2 sites) and heptachlor epoxide and DDE (1 site each). Of the 12 sites with 

dieldrin PEL exceedances, 9 were from the Great Miami 

River Basin. Sediment from the Great Miami River at RM 

79.95 had the highest concentration (67.0 μg/kg), followed 

by sediment from the Great Miami River at RM 31.19 (60 

μg/kg). Two sites, Little Miami River at Dolly Varden Road 

(RM 98.98) and Anderson Fork at Winchester Trail (RM 

4.90), were the only sites to exceed PELs for dieldrin in the 

Little Miami Basin with concentrations of 16.6 μg/kg and 

8.01 μg/kg respectively. Concentrations of dieldrin and heptachlor epoxide exceeded the most TELs (seven each), followed by lindane (four), DDE (three), and DDD and endrin 

Synthetic organic compounds 17 
18 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins

Figure 7. Location of streambed-sediment samples exceeding Canadian Sediment-Quality Guideline Probable Effect Levels 

(PELs) and fish tissue samples exceeding New York Fish Flesh Criteria (NYFFC) for organochlorine insecticides in the Great and 

Little Miami River Basins, Ohio and Indiana, 1990–98.

(one site each). Six of the seven dieldrin guideline exceedances were from the Little Miami River Basin, and six of

seven heptachlor epoxide exceedances also were from the 

Little Miami River Basin. 

Fish tissue. Of the 27 organochlorine insecticides analyzed, 11 were detected at MIAM fish-tissue sites. Dieldrin,

DDE, trans-nonachlor, and cis-chlordane were detected at 

all eight sites. Concentrations of dacthal (5 μg/kg) and 

oxychlordane (49 μg/kg) were highest at the Great Miami 

River at Tipp City. The Mad River had the highest concentrations of cis-nonachlor (40 μg/kg), trans-nonachlor (230 

μg/kg), p,p’-DDD (31 μg/kg), p,p’-DDE (280 μg/kg), cischlordane (130 μg/kg), and trans-chlordane (45 μg/kg). 

Total DDT (primarily DDE) in fish tissue at the Mad River

was detected at a concentration (311 μg/kg) that exceeds the 

NYFFC guideline of 200 μg/kg. Organochlorine insecticides detected at MIAM sites were compared to 1991 and 

1994 national NAWQA summary statistics for agricultural, 

urban, and mixed-land-use settings (fig. 8). Mad River concentrations of cis- and trans-chlordane, cis and trans-nonachlor, exceeded national NAWQA maximum 

concentrations for agricultural sites. The concentration at 

MILES

KILOMETERS

Troy

EXPLANATION

LAND USE

 Urban

 Other

ORGANOCHLORINE

 INSECTICIDES–Number

 of exceedances at site

 Streambed sediment

 1

 2

 none

 

 Fish-tissue

 1

 none
Great Miami River at Hamilton exceeded the maximum occurred. The Mad River had the eight highest cis-chlorconcentration for hexachlorobenzene for mixed-land-use dane concentrations, five of which were on the main stem. 

sites but was below NYFFC guidelines. The only NYFFC guideline exceeded was for the total DDT 

For state-agency data, the most commonly detected concentration at Mad River RM 6.2 (203 μg/kg). 

organochlorine insecticides in fish tissue were dieldrin, Possible sources of organochlorine insecticides in seditrans-chlordane, DDE, and cis-chlordane detected at 89, 82, ment and tissue. In the study unit, dieldrin was the most com81, and 77 percent of the sites, respectively. Four sites from monly detected organochlorine in sediment and fish tissue, 

the Little Miami River main stem had the highest concentra- and concentrations exceeded the most sediment PELs. High 

tions of dieldrin (45.2, 50.5, 68.7, and 88.0 μg/kg). The dieldrin exceedances in the study unit are likely because of 

highest trans-chlordane concentrations were on the Great its persistence and widespread use in the past, especially in 

Miami River main stem downstream from Middletown and regions high in corn production. Approximately 84 percent 

Dicks Creek (RM 48 and 47.5). The highest concentrations of the farmland in the study unit is used for crop production, 

of DDE were measured at the Little Miami River RM 3.5 particularly corn, wheat, and soybeans (Debrewer and othand RM 18.5 (149 μg/kg and 101 μg/kg) and Mad River RM ers, 2000). Dieldrin is a byproduct of the insecticide aldrin; 

6.2 and RM 17.3 (160 μg/kg and 100 μg/kg). The most per- therefore, elevated dieldrin concentrations in the study unit 

sistent metabolite of DDT is p,p’-DDE, and the dominance may reflect a combination of aldrin and dieldrin residues 

of this metabolite may indicate that DDT is late in the deg- (Nowell, 1999). The second most commonly detected orgaradation process and that no recent contamination has nochlorine insecticide in sediment, cis-chlordane, was the 

cis-CHLORDANE 

trans-CHLORDANE 

p,p'-DDD 

p,p'-DDE 

DIELDRIN 

HEXACHLOROBENZENE 

cis-NONACHLOR 

trans-NONACHLOR 

OXYCHLORDANE 

TOTAL PCB 

1 10 100 1,000 10,000 100,000 

CONCENTRATION, IN MICROGRAMS PER KILOGRAM 

EXPLANATION 

FISH-TISSUE GUIDELINES 

Less than NYFFC 

Greater than NYFFC 

SUMMARY STATISTICS 

NAWQA composite range 

NAWQA median for agricultural sites 

NAWQA median for mixed sites 

NAWQA median for urban sites 

NAWQA minimum concentration less than the detection limit 

SAMPLING SITE 

Agriculture 

Urban 

Mixed 

Figure 8. Concentrations of selected organochlorine insecticides and total PCBs at MIAM fish-tissue sites compared to New 

York Fish Flesh Criteria (NYFFC) and selected 1991 and 1994 national NAWQA study units. 

Synthetic organic compounds 19 
fourth most common organochlorine insecticide detected in 

fish tissue. Of chlordane components, cis-chlordane is one 

of the most abundant (Nowell, 1999). Agricultural and 

urban land have both contributed to concentrations of this 

persistent compound in the study unit. Chlordane is commonly associated with urban lawn and garden pesticides and 

household termite control, as well as an agricultural pesticide, particularly for corn (Eisler, 1985–99). Once in the 

water column, chlordane readily adsorbs to suspended solids and sediments. Chlordane concentrations tend to be 

higher in sediments with high organic content (Eisler, 1985– 

99). Additional data would be needed to determine whether 

organic content is a factor affecting sediment chlordane concentrations in the study unit. Eisler (1985–99) states that 

proximity to pest-control application, fish species feeding 

habits, and high lipid content are factors in determining 

chlordane concentrations in biota. Lipid percent in the study 

unit correlated positively and significantly with chlordane 

concentration (rho 0.56, p = 0.0016) and may be a factor 

affecting high chlordane detection in fish tissue. 

There was no geographic overlap in the sampling 

sites where sediment and fish-tissue organochlorine insecticide guidelines were exceeded. Few organochlorine insecticides exceeded guidelines in sediment. Exceedances were 

generally widespread throughout the study unit, with a few 

concentrated areas on Little Beaver Creek, the Whitewater 

River below Richmond, and below the confluence of the 

Stillwater and Mad Rivers with the Great Miami River. In 

tissue, organochlorine insecticides were commonly detected 

throughout the study unit. The only tissue-guideline exceedances for DDT were at the Mad River. Higher concentrations of chlordane and DDT were detected at the Mad River 

sites by both MIAM and state-agency investigations, and 

chlordane concentrations exceeded national NAWQA maximum concentrations. 

Polychlorinated biphenyls . PCBs consist of 209 

synthetic halogenated aromatic hydrocarbons, some of 

which are more commonly known by their industrial trade 

name, Arochlor. Since 1979, nearly all uses of PCBs and 

their manufacture have been prohibited in the United States 

(Eisler, 1985–99). PCBs are especially toxic to wildlife 

because of their ability to bioaccumulate and biomagnify 

through the food chain. 

Streambed sediment. PCBs were not detected at any of 

the eight MIAM sediment sites. PCBs were detected at 12 

percent of the sites from the 1991 and 1994 national 

NAWQA studies, with an average concentration of 

35.6 μg/kg. PELs were exceeded in national NAWQA sites 

from mixed and urban land use but not in sites from agricultural land use. 

In state-agency data, PCBs were detected at 17 of 

188 sites (9 percent), 6 of which exceeded the PEL of 

277 μg/kg (fig. 9). All elevated PCB concentrations in sediment were from the Great Miami River main stem between 

Dayton and Hamilton, with the exception of a single site 

from Little Beaver Creek, a tributary to the Little Miami 

River. The two highest concentrations were detected at 

Dicks Creek RM 2.51 and RM 0.93, at 18,330 μg/kg and 

14,300 μg/kg, respectively. TELs were exceeded at 11 sites 

(5 percent), 5 from the Great Miami River main stem. 

Fish tissue. PCBs were detected at all MIAM fishtissue sampling sites except for the Mad River. Detected 

concentrations ranged from 160 μg/kg in the Stillwater 

River to 2,300 μg/kg in the Great Miami at Hamilton. All 

MIAM sites, except the Mad River, exceeded the NYFFC 

guideline concentration of 110 μg/kg for the protection of 

fish-eating wildlife. PCBs detected at MIAM fish-tissue 

sites from agricultural, urban, and mixed-land-use settings 

were compared to 1991 and 1994 national NAWQA concentrations (fig. 8). With the exception of Mad River, concentrations of PCBs at all MIAM sites exceeded national 

medians. Concentrations from the Stillwater and East Fork 

Little Miami River sites exceeded the 90th percentile of all 

national NAWQA agricultural land-use settings, and those 

at the Whitewater, Great Miami River at Tipp City, and 

Great Miami River at Hamilton exceeded the 95th percentile for their respective land-use settings. 

In state-agency data, concentrations of PCBs at 29 of 

36 sites sampled (81 percent) exceeded NYFFC guidelines. 

Exceedances were found at 7 of 8 (88 percent) Little Miami 

River Basin sites and at 22 of 28 (79 percent) Great Miami 

River Basin sites. Sites with the highest concentrations were 

from the Little Miami at Cincinnati-Beechmont Avenue 

(1,049 μg/kg), Mad River at Huffman Dam (860 μg/kg), and 

Great Miami River downstream from Dicks Creek 

(839 μg/kg). Sites with elevated concentrations were in 

heavily industrialized areas clustered on the Mad River near 

Springfield and on the Great Miami River between Middletown and Hamilton. All state-agency sites from the Mad 

River had concentrations of PCBs that exceeded the 

NYFFC guideline. 

Possible sources of PCBs in sediment and tissue. No geographic overlap for PCB exceedances was evident between 

sediment and tissue sites. PCB concentrations in tissue were 

detected in 81 percent of state-agency sites and 88 percent 

of MIAM sites. NYFFC guidelines were exceeded at 36 of 

44 sites collected throughout the study unit. Five of six sites 

with sediment PCB exceedances were on the Great Miami 

River main stem between Dayton and Hamilton, compared 

to tissue exceedances, which were common and widespread 

throughout the study unit. PCBs are hydrophobic and lipophilic (having a strong affinity for lipids), which may be 

important factors contributing to the high detection of PCBs 

in fish tissue in the study unit. Hydrophobicity is typically 

measured by the n-octanol:water partition coefficient (Kow), 

which is related to the accumulation of nonpolar organic 

compounds in an organism (Crawford and Luoma, 1994; 

Okanagan University College, 2002). A higher log Kow 

value, as found in arochlors 1242, 1254, and 1260, indicates 

that the compound is more hydrophobic, and has a 

20 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
Synthetic organic compounds 21

Figure 9. Location of sediment samples exceeding Canadian Sediment-Quality Guideline Probable Effect Levels (PELs) and 

fish-tissue samples exceeding New York Fish Flesh Criteria (NYFFC) for polychlorinated biphenyls in the Great and Little Miami

River Basins, Ohio and Indiana, 1990–98.

higher potential for biological uptake (Eisler, 1985–89). 

PCBs can accumulate in the lipid-containing tissue of 

aquatic organisms after uptake across gill membranes or by

active uptake through the ingestion of food (Eisler, 1985–

99). Lipid percent correlated positively and significantly

with PCB concentration in fish tissue in the MIAM study 

unit (rho = 0.58, p = 0.0028). Between 1985 and 1995, four

entities were responsible for 10 or more unauthorized 

releases of contaminants, including PCB materials in the 

Great Miami River Basin between Dayton and the mouth 

near Cincinnati (Ohio Environmental Protection Agency, 

1997a). PCB contamination was noted at four NPL sites in

the study unit: an incinerator, two landfills, and a chemicalwaste transfer and disposal facilty.

MILES

KILOMETERS

Troy

Middletown

Hamilton

EXPLANATION

LAND USE

 Urban

 Other

TOTAL POLYCHLORINATED

 BIPHENYLS–Number

 of exceedances at site

 Streambed sediment

 1

 none

 

 Fish-tissue

 1

 none

Mad

Buck

Springfield
Semivolatile organic compounds in streambed sediment. SVOCs include polycyclic aromatic hydrocarbons 

(PAHs), azaarenes, phthalates, phenols, and chlorinated 

compounds. SVOCs are typically characterized by low to 

moderate vapor pressures and low solubilities in water. 

Many are toxic compounds that accumulate in the streambed sediment and, at high concentrations, may become 

harmful to benthic organisms. PAHs do not bioaccumulate 

in fish; therefore, tissue samples were not analyzed for 

SVOCs (Crawford and Luoma, 1994). 

Of the 65 SVOCs analyzed in MIAM sediments, 32 

were detected. Of these 32, 15 PAHs, 6 alkyl PAHs, 4 phthalates, 2 phenols, 2 azaarenes, 1 quinone, 1 sulfurous-PAH, 

and 1 nitro-aromatic were detected. The most commonly 

detected SVOCs were benzo[a]pyrene, chrysene, bis(2-ethylhexyl)phthalate, fluoranthene, indeno[1,2,3-cd] pyrene, 

and phenanthrene, which were detected at all eight MIAM 

sites. The Little Miami River at Milford and Holes Creek 

sites had the most compounds detected, (28), followed by 

BENZ[A]ANTHRACENE 

BENZO[A]PYRENE 

p-CRESOL 

2,6-DINITROTOLUENE* 

FLUORANTHENE 

INDENO[1,2,3-CD]PYRENE 

PHENANTHRENE 

PYRENE 

the Great Miami River at Hamilton, with 26. Among the 

agricultural sampling locations, Great Miami at Tipp City 

had the most compounds detected (22), followed by Mad 

River (19), East Fork Little Miami River (18), and Stillwater 

River and Whitewater River (14 at each site). Concentrations of pyrene (518 μg/kg) and phenanthrene (516 μg/kg) 

concentrations were the highest among the PAHs and were 

detected at Great Miami River at Hamilton. Phenanthrene 

was the only PAH to exceed a PEL (515 μg/kg). Eight 

SVOCs were detected at concentrations at or above a TEL. 

The Little Miami at Milford and the Great Miami at Hamilton had the most TEL exceedances (6) followed by Holes 

Creek and Great Miami at Tipp City (5), Mad River (4), and 

East Fork Little Miami River (2). 

The increased number of detections and higher concentrations of SVOCs in samples from at the mixed-landuse and urban sites is comparable to the findings of Lopes 

and Furlong (2001) in their analyses of 1991 national 

NAWQA SVOC data (fig. 10). Nationally, PAHs were 

1 10 100 1,000 10,000 100,000 

CONCENTRATION, IN MICROGRAMS PER KILOGRAM 

EXPLANATION 

BED-SEDIMENT-QUALITY GUIDELINES 

Less than Threshold Effect Level (TEL) 

Greater than TEL and less than Probable Effect Level (PEL) 

Greater than PEL 

No guidelines 

SUMMARY STATISTICS 

NAWQA composite range 

NAWQA 75th percentile 

NAWQA minimum concentration less than the detection limit 

* National 75th percentile less than the detection limit 

SAMPLING SITE 

Agriculture 

Urban 

Mixed 

Figure 10. Concentrations of selected semivolatile organic compounds at MIAM streambed-sediment sites compared to 

Canadian Sediment-Quality Guideline Probable Effect Levels (PELs) and data from selected 1991 NAWQA study units. 

(Concentrations below 50 μg/kg are estimated values.) 

22 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins 
Synthetic organic compounds 23

detected most frequently and at highest concentrations at 

the urban sites. All MIAM SVOC detections at mixed and 

urban sites exceeded the national 75th percentile. Concentrations of p-cresol and phenanthrene at the Great Miami 

River at Hamilton exceeded 90th-percentile concentrations. 

Concentrations of diethyl phthalate at the East Fork Little 

Miami River (1.7 μg/kg, estimated) and 2,6-dinitrotoluene 

(196 μg/kg) exceeded the maximum concentration of <50 

μg/kg and 93 μg/kg, respectively.

For state-agency data, the most commonly detected 

SVOCs were pyrene, fluoranthene, benzo[k]fluoranthene, 

benzo[b]fluoranthene, and phenanthrene (67, 65, 68, 60,

and 54 sites, respectively). Forty-six of 155 sites exceeded 

the PEL for SVOCs (fig. 11). A higher proportion of 

exceedances was found in the Great Miami River Basin (25 

of 64 sites, 39 percent) than in the Little Miami River Basin 

(21 of 91 sites, 23 percent), and three or more guidelines 

were commonly exceeded at each site. The compounds that 

exceeded PELs most often were PAHs: pyrene (43 sites), 

Figure 11. Location of streambed-sediment samples exceeding Canadian Sediment-Quality Guideline Probable Effect Levels 

(PELs) for semivolatile organic compounds in the Great and Little Miami River Basins, Ohio and Indiana, 1990–98.

MILES

KILOMETERS

Troy

Dayton

Hamilton

EXPLANATION

LAND USE

Urban

Other

SEMIVOLATILE ORGANIC

COMPOUNDS IN

STREAMBED

SEDIMENT–Number of

exceedances at site

1-2

3-4

5-6

7-8

none
24 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins

phenanthrene (31 sites), chrysene (26 sites), benzo[a]pyrene 

(18 sites), and fluoranthene (17 sites). The USEPA lists all 

of these compounds as hazardous substances. The concentrations of eight of eleven SVOCs detected at the Great 

Miami River at RM 51.3 exceeded PELs. Seven of 11 compounds detected exceeded PELs at Sycamore Creek (RM 

0.05), a Little Miami River tributary. TELs were most commonly exceeded for fluoranthene (66 sites), pyrene (58 

sites), and chrysene (40 sites). 

The higher occurrence of SVOCs, particularly PAHs, 

at the MIAM urban and mixed-land-use sites compared to 

agricultural sites can be expected. These sites have the highest percentages of urban land use, and many SVOCs are 

byproducts of incomplete fossil-fuel combustion and industrial processes. Other sources of SVOCs in the study unit 

include NPL landfills, incinerators, and liquid-waste disposal facilities. The high detection of PAHs compared to 

phthalates, phenols, and azaarenes is most likely due to their 

physical and chemical properties. PAHs are the most hydrophobic and persistent compounds among the SVOCs and 

are common in fossil fuels. Because of their low solubilities, PAHs tend to partition into sediments and soils. In the 

study unit, SVOC PELs were frequently exceeded along the 

Great Miami River main stem south of Dayton and Middletown, and in Little Beaver Creek and Lytle Creek in the 

upper Little Miami River Basin. The large number of PEL 

exceedances at the Great Miami River RM 51.3 is likely due 

to its proximity to an outfall from a major steel company. 

Discharge from the outfall consists of effluents from the 

north terminal treatment plant, blast furnace/sinter plant, 

wastewater treatment plant, and storm water runoff (Ohio 

Environmental Protection Agency, 1997a). Potential 

sources of contaminants contributing to high PEL exceedances at Sycamore Creek include a wastewater-treatment 

plant and sanitary sewer overflows, spills, urban runoff, and 

sludge deposits (Ohio Environmental Protection Agency, 

1997a).

Summary 

In summer 1998, streambed-sediment and fish-tissue samples were collected from eight sites in the Great and Little 

Miami River Basins (MIAM) study unit of the National 

Water-Quality Assessment (NAWQA) Program. Samples 

were analyzed for trace elements and synthetic organic 

compounds including organochlorine insecticides, polychlorinated biphenyls (PCBs), and other semivolatile 

organic compounds (SVOCs). Data from investigations by 

the state agencies, Ohio Environmental Protection Agency 

(OEPA) and Indiana Department of Environmental Management (IDEM), were incorporated to gain a better perspective of the occurrence and distribution of contaminants 

in the study unit, and all data were compared to appropriate 

guidelines to identify elevated contaminant concentrations. 

Guideline exceedances were plotted on distribution maps to 

identify sites of potential concern for wildlife health and 

areas potentially in need of restoration.

All trace elements of interest (arsenic, cadmium, 

chromium, copper, lead, mercury, nickel, selenium, and 

zinc) were detected in sediment at the MIAM sites, but no 

sediment-quality guidelines were exceeded. The most commonly detected trace elements in state-agency sites were 

zinc, copper, arsenic and cadmium. Probable Effect Levels 

(PEL, concentrations above which adverse effects are frequently anticipated) in sediment were exceeded at 32 stateagency sites. In sediment, PELs were exceeded for zinc (16 

sites), lead (15 sites), arsenic (5 sites), cadmium (5 sites), 

chromium (3 sites), and mercury (1 site). Areas of higher 

trace-element concentrations include selected reaches of the 

Mad River near Springfield, Dicks Creek, and the upper 

Great Miami River main stem near Troy.

Arsenic, cadmium, copper, mercury, selenium, and 

zinc were detected at all MIAM fish-tissue sites. Lead was 

detected at all but the Mad River site. For state-agency data, 

mercury, cadmium, and lead were detected most often in 

fish tissue. Detections of trace elements were most frequent 

on the Mad River near Springfield; Great Miami River main 

stem near the cities of Middletown, Hamilton and north of 

Dayton; and along the main stem of the Little Miami River. 

Urban and agricultural land uses were both found to 

contribute to trace-element concentrations in the study unit. 

Potential sources of trace elements in the study unit include 

motor-vehicle parts and electronics manufacturers, steel 

mills, landfills, agricultural pesticides, and feedlots.

Few organochlorine insecticides were detected in 

sediments and tissue throughout the study unit. At MIAM 

sites, 31 compounds were analyzed for in sediment, with 5 

detected: trans-nonachlor, heptachlor epoxide, cis-chlordane, trans-chlordane, and dieldrin. Heptachlor epoxide 

was the only insecticide to exceed a recommended guideline: a concentration of 1.1 μg/kg detected at the urban site, 

Holes Creek, exceeded the Threshold Effect Level (TEL, 

the concentration below which adverse effects are rarely 

anticipated) of 0.6 μg/kg. All MIAM agricultural sites 

exceeded the national NAWQA median for dieldrin. At 

state-agency sites, organochlorine insecticides were 

detected at 25 sites at levels that may have adverse effects 

on aquatic organisms. Exceedances of PEL guidelines were 

more frequent on the Great Miami River south of Dayton 

and Little Beaver Creek, a Little Miami River tributary. 

PELs were exceeded for dieldrin, total chlordane, lindane, 

heptachlor epoxide, DDT, and DDE. Dieldrin PELs and 

TELs were exceeded most often.

Twenty-seven organochlorine insecticides were analyzed for in MIAM fish-tissue samples, and 11 were 

detected. Dieldrin, DDE, trans-nonachlor, and cis-chlordane were detected at all eight sites. Concentrations of total 
References 25

DDT at Mad River exceeded the New York Fish Flesh Criteria of 200 μg/kg. Concentrations of trans-chlordane, cischlordane, trans-nonachlor, and cis-nonachlor at the Mad 

River exceeded previous study-unit maximum concentrations for agricultural sites. For state-agency data, the most 

commonly detected organochlorine insecticides were dieldrin, trans-chlordane, DDE, and cis-chlordane. Sites in the 

Mad River Basin had the highest concentration of DDE and 

the eight highest cis-chlordane concentrations; the only 

NYFFC guideline exceedances for total DDT were found at 

the Mad River near Springfield and Mad River RM 6.2 sites.

Dieldrin was the most commonly detected organochlorine insecticide in sediment and fish tissue, and its 

PEL was the most frequently exceeded in sediment. More 

organochlorine insecticides were detected in tissues than in 

sediment; however, more guidelines were exceeded in sediment. There was no geographic overlap of sediment and 

fish-tissue sites with respect to elevated organochlorine 

insecticide concentrations. Exceedances were generally 

widespread throughout the study unit, with a few concentrated areas on Little Beaver Creek, the Whitewater River 

below Richmond, and below the confluence of the Stillwater and Mad Rivers with the Great Miami River. 

PCBs were not detected at any of the eight MIAM 

sediment-sampling locations. PCBs were detected at 17 

(9 percent) state-agency sites, and concentrations at 6 sites 

exceeded the PEL. All elevated PCB concentrations in sediment were from the Great Miami River Basin between Dayton and Hamilton, with the exception of a single site on 

Little Beaver Creek, a tributary to the Little Miami River. 

Concentrations of PCBs in fish tissue exceeded the 

national median and NYFFC guidelines at all MIAM sites 

except for the Mad River. Concentrations at the Whitewater 

River, Great Miami at Tipp City, and Great Miami at Hamilton sites exceeded the national NAWQA 95th percentile for 

their respective land uses. At state-agency sites, 81 percent 

(36 of 44) of sites sampled exceeded NYFFC guidelines, 

and all samples from the Mad River were at concentrations 

that exceeded guidelines. Concentrated areas with guideline 

exceedances were on the Mad River near Springfield and on 

the Great Miami River main stem between Middletown and 

Hamilton.

No distinct geographic overlap for PCB exceedances 

is evident between sediment and fish-tissue sites. Overall, 

fish tissue appeared to be a better indicator of PCB contamination than streambed sediment. PCB exceedances in fish 

tissue were common and widespread throughout the study 

unit and in similar geographic distributions to trace-element 

detections. Local sources of PCBs include incinerators, 

landfills, and chemical-waste transfer and disposal facilities.

 Of the 62 SVOCs analyzed for in MIAM sediments, 

32 were detected. Most commonly detected SVOCs were 

benzo[a]pyrene, chrysene, bis(2-ethylhexyl)phthalate, fluoranthene, indeno[1,2,3-cd] pyrene, and phenanthrene, which 

were detected at all eight sites. Sites with the most SVOCs 

(28) detected were from the Little Miami River at Milford 

mixed-land-use site and the Holes Creek urban site, followed by the Great Miami River at Hamilton mixed-landuse site. Phenanthrene at the Great Miami River at Hamilton 

was the only PEL exceedance for SVOCs in the MIAM 

study. All detections from MIAM mixed- and urban-landuse sites exceeded the national NAWQA 75th percentile. In 

state-agency sites, the most commonly detected SVOCs 

were pyrene, fluoranthene, benzo[k]fluoranthene, 

benzo[b]fluoranthene, and phenanthrene. SVOC concentrations exceeded PELs at 46 sites. PAH guidelines, particularly for pyrene, were exceeded most often. SVOC PELs 

were frequently exceeded along the Great Miami River 

main stem from Dayton to south of Hamilton and in the 

Upper Little Miami River Basin in Greene County. Three or 

more SVOC guidelines were commonly exceeded per site. 

Point sources of SVOCs in the study unit include NPL landfills, an incinerator, liquid-waste disposal facility, and a 

major steel manufacturer.

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28 Trace Elements and Synthetic Organic Compunds in Streambed Sediment and Fish Tissue, Great and Little Miami River Basins

Appendix A

Results of a national assessment of mercury contamination of aquatic ecosystems

In 1998, the MIAM was one of 21 NAWQA study units 

across the United States to participate in a national assessment of mercury contamination of aquatic ecosystems 

(Krabbenhoft and others, 1999). Water, sediment, and 

smallmouth bass fish-fillet samples were collected at 106 

sites representing a variety of land uses. Seven sites were 

sampled in the MIAM study area. Water and sediment samples were analyzed for total mercury and methylmercury; 

fish-fillets were analyzed for total mercury only. 

Concentrations of total mercury (3.00 ng/L) and 

methylmercury (0.19 ng/L) in MIAM water samples were 

highest at the Great Miami River at Hamilton site, and they 

exceeded the national medians of 2.28 ng/L and 0.06 ng/L, 

respectively (fig. A1, table A1). Sediment concentrations of 

methylmercury ranged from 0.17 ng/g in the Stillwater 

River to 1.54 ng/g at Mad River; all sites were below the 

national median with the exception of Great Miami River at 

Hamilton and Mad River. All MIAM sediment concentrations of total mercury were below the national median with 

the exception of the mixed-land-use site Great Miami River 

at Hamilton. MIAM fish-fillet concentrations ranged from 

0.04 μg/g at Little Miami River at Milford to 0.52 μg/g at 

the East Fork Little Miami River at Williamsburg. All three 

fillets from the agricultural site East Fork Little Miami 

River exceeded the national median for smallmouth bass fillet composite of 0.205 μg/g. The national median was also 

exceeded in fillet samples from the Mad River (0.27 μg/g) 

and Little Miami River at Milford (0.278 μg/g). The Food 

and Drug Administration action level (1 μg/g) for mercury 

concentrations in fish fillets was not exceeded at any MIAM 

site (Food and Drug Administration, 2003).

 Statistical analyses of methylmercury concentrations 

from the 21 study units found stronger correlations between 

fish fillet and water than between fish fillet and sediment 

(Brumbaugh and others, 2000). At low total mercury concentrations, methylmercury production and total mercury 

concentrations are proportional (Krabbenhoft and others, 

1999). Further information on this study can be found in 

Krabbenhoft and others (1999) and Brumbaugh and others 

(2000).

Mercury has no known biological function and is 

potentially hazardous to all living organisms. For fish species, it is the most toxic trace element. Fish exposure is predominantly through the diet but also may be through the 

gills. Mercury, unlike other trace elements, has a tendency 

to accumulate at higher concentrations in fish muscle than 

in liver or kidneys (Maret and Dutton, 1998). Mercury bioconcentrates and then biomagnifies throughout the food 

chain; therefore, predator species at the top of the food web 

generally have higher concentrations in their bodies than 

their prey do. Effects of mercury poisoning in fish include 

reduced reproductive success, impaired growth, and developmental and behavioral abnormalities (Eisler, 1985–99). 

Methylmercury is the most common organic form of mercury. It has a strong affinity for proteins and accounts for 

90–100 percent of the total mercury found in fish tissue 

(Eisler, 1985–99) . 

Appendix references

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contamination of aquatic ecosystems along multiple 

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Water-Resources Investigations Report 98–4254, 55 p.
Appendix A 29

Table A1. Mercury concentrations in fish fillets, bed sediment, and surface water at selected sampling locations in the Great and Little

Miami River Basin

[g, grams; μg/g, microgram per gram; ng/g, nanograms per gram ; ng/L, nanograms per liter. Additional station location information can be found in figure 

1 and table 1 of the main text.]

Station number Number 

of fish 

Fish fillet Bed sediment Surface water

Mean 

weight

(g)

Age

(years)

Mercury 

(μg/g) 

Total mercury 

(ng/g)

Methyl 

mercury

 (ng/g)

Total 

mercury 

(ng/L)

Methyl 

mercury 

(ng/L)

03245500 3 55 1.5 0.04 9.20 0.45 1.57 0.05

03245500 1 698 5.5 0.28 9.20 0.45 1.57 0.05

03246400 2 386 3.5 0.36 13.30 0.24 2.09 0.07

03246400 1 107 2.5 0.20 13.30 0.24 2.09 0.07

03246400 1 608 4.5 0.52 13.30 0.24 2.09 0.07

392246084340100 1 345 3.5 0.11 87.20 0.67 3.00 0.19

393259085101200 1 80 2.5 0.14 11.70 0.43 0.81 0.03

393259085101200 1 129 2.5 0.13 11.70 0.43 0.81 0.03

393259085101200 2 257 4 0.20 11.70 0.43 0.81 0.03

395433084175300 3 130 2.5 0.18 34.00 0.17 2.10 0.05

395433084175300 1 284 3.5 0.14 34.00 0.17 2.10 0.05

395534084091400 4 178 3.5 0.12 31.40 0.34 2.52 0.05

395534084091400 1 518 5.5 0.27 30.80 1.54 0.79 0.08 SEDIMENT, IN NANOGRAMS PER GRAM WATER, IN NANOGRAMS PER LITER FILLET, IN MICROGRAMS PER GRAM

0.01 0.1 1 10 100 1,000 10,000

CONCENTRATION

Total Mercury

Methylmercury

Total Mercury

Methylmercury

Total Mercury

NATIONAL RANGE

NATIONAL MEDIAN

AGRICULTURAL SITES

URBAN SITES

MIXED-LAND-USE SITES

EXPLANATION

Figure A1. Comparison of mercury concentrations in fish-fillet samples in the Great and Little Miami River Basins 

study unit to range and median concentrations from 21 NAWQA study units (MIAM included). (Fish-tissue fillet 

concentrations are shown for each fish analyzed.)

Appendix A