&EPA
United States
Environmental Protection
Agency
Permits Division
(EN-336)
Washington DC 20460
Environmental Research
Laboratory
Duluth MN 55804
OWEP 84-01
EPA-600/3-84-080
August 1984
Research and Development
Effluent and
Ambient Toxicity
Testing and
Instream
Community
Response on the
Ottawa River,
Lima, Ohio
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EPA-600/3-84-080
August 1984
Effluent and Ambient Toxicity
Testing and Instream Community
Response on the Ottawa River,
Lima, Ohio
by
Donald I. Mount, Nelson A. Thomas, Teresa J. Norberg," Michael T. Barbour,"
Thomas H. Roush," and William F Brandes0
aU.S. Environmental Protection Agency, Environmental Research Laboratory,
6201 Congdon Boulevard, Duluth, Minnesota 55804.
"EA Engineering, Science, and Technology, Inc. (formerly called Ecological Analysts, Inc.),
Hunt Valley/Loveton Center, 15 Loveton Circle, Sparks, Maryland 21152
°U.S. Environmental Protection Agency, Office of Water Enforcement, Permits Division (EN-336),
401 M Street SW, Washington, D.C. 20460
Environmental Research Laboratory
Office of Research and Development
U.S. Environmental Protection Agency
Duluth, Minnesota 55804
Permits Division (EN-336)
Office of Water Enforcement and Permits
U.S. Environmental Protection Agency
Washington, D.C. 20460
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Notice
This document has been reviewed in accordance with U.S. Environmental
Protection Agency policy and approved for publication. Mention of trade names
or commercial products does not constitute endorsement or recommendation
for use.
ii
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List o( Contributors
Toxicity of Effluents and Receiving Water, 1982
Donald I. Mount8 and Teresa J. Norberg8
Toxicity of Effluents and Receiving Water, 1983
Donald I. Mount8 and Teresa J. Norberg8
Dilution Analysis of the STP, Refinery, and Chemical Plant
Jonathan C. Yostb
Periphytic Community, 1982 Survey
Ronald J. Bockelmanb
Benthic Macroinvertebrate Community, 1982 Survey
Michael T. Barbourb and Anna T. ShaughnessyC
Fish Community, 1982 Survey
David P. Lemarieb and Michael T. Barbourb
Fish Caging Stud~
David P Lemarie
Benthic Macroinvertebrate Community, 1983 Survey
Thomas H. Roush8, Teresa J. Norberg8, and Michael T. Barbourb
Fish Community, 1983 Survey
Thomas H. Roush8, Teresa J. Norberg8, and Michael T. Barbourb
Zooplankton Community, 1983 Survey
Thomas E. Roush 8, Teresa J. Norberg8, and Michael T. Barbourb
Comparison of Laboratory Toxicity Data and
Receiving Water Biological Impact
Nelson A. Thomas 8 and Donald I. Mount8
.u.s. Environmental Protection Agency. Env.ronmental Research Laboratory-Duluth. 6201 Congdon Blvd.,
Duluth. Minnesota 55B04.
bEA Engineering. Science, and Technology, Inc. (formerly called Ecological Analysts, Inc.), Hunt Valley/Loveton
Center, 15 Loveton Circle. Sparks, Maryland 21152
cEA Englneenng, Science, and Technology, Inc. Current Address Mart.n Manetta Environmental Systems, 9200
Rumsey Rd., Columbia, Maryland 21045
iii
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Contents
Page
List of Contributors. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. III
List of Tables. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. vii
List of Figures. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .
x
Foreword. . . . . . . . . . . . .
............................................. XII
Executive Summary. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . xiv
Quality Assurance. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. xv
1.
2.
Introduction. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 1-1
Study Design. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 2-1
2.1 Toxicity Testing Study Design. . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 2-1
2.2 Field Survey Study Design. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 2-2
2.3 Approach to Integration of Laboratory and Field Efforts. . . . . . .. 2-3
Site Description. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 3-1
3.
4. Toxicity of Effluents and Receiving Water, 1982. . . . . . . . . . . . . . . . . . .. 4-1
4.1 Chemical/Physical Conditions. . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 4-1
4.2 Results of Fathead Minnow Growth Test..................... 4-1
4.3 Results of Reproductive Potential Tests Using Ceriodaphnia . . .. 4-2
4.4 Evaluation of Toxicity Impact. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 4-6
5. Toxicity of Effluents and Receiving Water, 1983. . . . . . . . . . . . . . . . . . .. 5-1
5.1 Results... . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 5-1
5.2 Discussion................................................ 5-3
6.
Dilution Analysis of the Sewage Treatment Plant,
Refinery, and Chemical Plant, 1982. . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 6-1
6.1 Sewage Treatment Plant. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 6-1
6.2 Refinery[[[ 6-3
6.3 Chemical Plant. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 6-4
6.4 Evaluation of Dilution Characteristics. . . . . . . . . . . . . . . . . . . . . . .. 6-5
Periphytic Community, 1982 Survey.............................. 7-1
7.1 Community Structure....................................... 7-1
7.2 Chlorophyll a and Biomass. . . . .. . . . . .. . .. .. . .. .. . ... . .. . .. .. 7-2
7.3 Evaluation of Periphytic Community Response.. .. . .... ... . . .. 7-3
Benthic Macroinvertebrate Community, 1982 Survey. . . . . . . . . . . . . .. 8-1
8.1 Community Structure. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 8-1
8.2 Spatial Trends in Key Taxa. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 8-4
8.3 Benthic and Zooplankton Drift Collections. . . . . . . . . . . . . . . . . . .. 8-6
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Contents (Continued)
Page
9. Fish Community, 1982 Survey................................... 9-1
9.1 Community Structure. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 9-1
9.2 Evaluation of Fish Community Response. . . . . . . . . . . . . . . . . . . .. 9-2
10. Fish Caging Study, 1982 Survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 10-1
10.1 In Situ Toxicity Testing.. .. .. . .. .. . .. .. .. .. . .. .. . .. . .. .... 10-1
11. Benthic Macroinvertebrate Community, 1983 Survey. . . . . . . . . . . . .. 11-1
11.1 Community Structure.................................... 11-1
11.2 Spatial Trends of Major Groups. . . . . . . . . . . . . . . . . . . . . . . . . .. 11-1
11.3 Comparison Between 1982 and 1983 Surveys. . . . . . . . . . . . .. 11-4
12. Fish Community, 1983 Survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 12-1
12.1 Community Structure. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 12-1
12.2 Comparison Between 1982 and 1983 Surveys. . . . . . . . . . . . .. 12-1
13. Zooplankton Community, 1983 Survey. . . . . . . . . . . . . . . . . . . . . . . . . .. 13-1
13.1 Community Structure. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 13-1
13.2 Evaluation of Zooplankton Community Response. . . . . . . . . . .. 13-1
14. Comparison of Laboratory Toxicity Data and
Receiving Water Biological Impact . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 14-1
14.1 Results of Integration Analyses. . . . . . . . . . . . . . . . . . . . . . . . . .. 14-3
14.2 1982-1983 Comparison. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 14-4
14.3 Calculation of Toxicity Reduction. . . . . . . . . . . . . . . . . . . . . . . . .. 14-6
References. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. R-1
Appendix A:
Appendix B:
Appendix C:
Appendix D:
Toxicity Test Methods.................................. A-1
Hydrological Methods. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. B-1
Biological Methods. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. C-1
C.1 Periphyton. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. C-1
C.2 Benthos.......................................... C-1
C-3 Fisheries......................................... C-2
C.4 Fish Caging Study. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. C-2
C.5 Zooplankton...................................... C-2
Support Biological Data. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. D-1
vi
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4-4
4-5
4-6
4-7
4-8
5-1
5-2
5-3
5-4
5-5
5-6
5-7
5-8
5-9
List o( Tables
Table
Page
4-1
Seven-Day Percent Survival of Larval Fathead Minnows
Exposed to Various Concentrations of Three Effluents in
Upstream Water, Lima, Ohio, 1982 . . . . . . . . . . . . . . . . . . . . . . . . 4-2
Average Concentration of Stream Water and Effluent Below
Each Discharge During the 1982 Testing Period. . . . . . . . . . . . . . 4-2
Mean Dry Weight of Larval Fathead Minnows Exposed to
Three Effluents at Various Concentrations, Lima, Ohio,
1982 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4-3
Seven-Day Percent Survival of Larval Fathead Minnows
Exposed to Refinery Waste Diluted with Two Different Dilution
Waters, Lima, Ohio, 1982 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4-3
Mean Dry Weight of Larval Fathead Minnows Exposed to
Refinery Effluents Diluted with Two Different Dilution Waters,
Lima, Ohio, 1982 ..................................... 4-3
Mean Young Per Original Female and Mean Percent Survival
of Adult Ceriodaphnia in Various Effluent Concentrations
Using Receiving Water for Dilutio." Lima, Ohio, 1982. . . . . . . . . . 4-4
Mean Young Per Original Female and Percent Survival of
Adult Ceriodaphnia in Refinery Effluent Concentrations Using
Lake Superior Water for Dilution, Lima, Ohio, 1982 ...........4-4
Mean Young Production and Percent of Survival of Ceriodaphnia
for the Ambient Toxicity Tests in 1982 ..................... 4-5
Chemistry Data for Three Effluents In Station 1 Water for
Fathead Minnow Larval Growth Tests, Lima, Ohio, 1983 ....... 5-1
Water Chemistry Data for Ambient Toxicity Test with Fathead
Minnows at VariOUS River Stations, Lima, Ohio, 1983. . . . . . . . . . 5-1
Final Dissolved Oxygen Concentrations for Ceriodaphnia Tests on
Effluents and Stream Station Water, Lima, Ohio, 1983 . . . . . . . . . 5-2
Seven-Day Percent Survival of Larval Fathead Minnows
Exposed to Vanous Concentrations of Three Effluents in
Station 1 Water, Lima, Ohio, 1983 ........................ 5-2
Mean Weight of Larval Fathead Minnows Exposed to Three
Effluents at Various Concentrations, Lima, Ohio,. 1983 . . . . . . . . . 5-3
Seven-Day Percent Survival of Larval Fathead Minnows
Exposed to Water from Vanous Stream Stations for Ambient
Toxicity, Lima, Ohio, 1983. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5-3
Mean Weight of Larval Fathead Minnows Exposed to Water
from Various Stream Stations for Ambient Toxicity, Lima,
Ohio, 1983 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5-3
Mean Young Per Female Ceriodaphnia and Mean 7-Day
Percent Survival of Original Test Animals Exposed to Various
Effluent Dilutions in Station 1 Water, Lima, Ohio, 1983 """" 5-4
Mean Young Per Female Ceriodaphnia and 7-Day Percent
Survival of Origmal Test Animals Exposed to Water from Various
Stream Stations for Ambient Toxicity, Lima, OhiO, 1983 . . . . . . . . 5-4
4-2
4-3
VII
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Table
5-10
5-11
6-1
6-2
6-3
7 -1
8-1
8-2
9-1
10-1
11 -1
11 -2
12-1
13-1
14-1
C-1
D-1
D-2
D-3
D-4
List of Tables (Continued)
Page
Geometric Mean of the Effect and No-Effect Concentration for
the Three Effluents and Two Test Species, Lima, Ohio, 1983 .... 5-4
Predicted Concentrations of STP and Refinery Effluent at
Near-Field Stations Based on Conductivity Measurements,
Lima, Ohio, 1983 ..................................... 5-5
Transect Locations for the Dye Dilution AnalysIs at Three
Sites on the Ottawa River, 1982 Survey. . . . . . . . . . . . . . . . . . . . 6-1
River Flows Upstream of the STP and Reported Discharge
Flows at Each Site, 1982 Survey. . . . . . . . . . . . . . . . . . . . . . . . . . 6-3
Ottawa River Flow and Percent Flow Contribution from the
Discharges on the Days of the Three Dye Surveys,
1982 Survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6-4
Summary of Perlphyton Composition, Diversity, and Standing
Crop on Natural Substrates in the Ottawa River,
September 1982 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 7-1
Average Density of the Most Aburdant Species at Each
Sampling Station, Ottawa River, 21 September 1982 . . . . . . . . . . 8-2
Density of Macroinvertebrates Collected from the Drift,
Ottawa River, 23 September 1982 ........................ 8-6
Results of Fisheries Survey of Ottawa River, Abundance by
Station, 24-26 September 1982 """"""""""""" 9-1
Results of Fish Caging Study, Ottawa River, 1982 Survey. . . . . . 10-1
Composition of the Benthic Community of the Ottawa River,
July 1983 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11-2
Abundance of Benthic Macroinvertebrates Collected from the
Ottawa River, July 1983 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 11-3
Results of Fish Collections in the Ottawa River, July 1983 ..... 12-1
Planktonic Organisms Collected from the Ottawa River,
July 1983 ..... . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13-1
Comparison of Toxicity and Biological Response. . . . . . . . . . . . . 14-1
Station Pool, Riffle Proportions, and Number of Seine
Hauls. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C-2
Abundance of Periphytic Algae on Natural Substrates
in the Ottawa River, September 1982 . . . . . . . . . . . . . . . . . . . . . . D-1
Chlorophyll a and Biomass Data and Statistical Results for
Periphyton Collected from Natural Substrates in the Ottawa
River, September 1982 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . D-2
Ranked Abundance Listing of All Macroinvertebrates Collected
from Ottawa River, 21 September 1982 .................... D-3
Shannon-Wiener Diversity Indices and Associated Evenness and
Redundancy Values and Community Loss Indices Calculated on
Benthic Data from Ottawa River, 1982 ..................... D-5
VIII
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Table
D-5
D-6
List of Tables (Continued)
Page
List of Fish Species and Families Collected from the Ottawa
River Near Lima, Ohio, 24-26 September 1982 . . . . . . . . . . . . . . . D-5
Shannon-Wiener Diversity Indices, Associated Evenness and
Redundancy Values, and Community Loss Indices Calculated on
Fisheries Data from Ottawa River, 1982 . . . . . . . . . . . . . . . . . . . . D-6
IX
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Figure
List of Figures
2-1
2-2
4-1
Page
Study area, Ottawa River, Lima, Ohio. . . . . . . . . . . . . . . . . . . . . . 2-2
Histogram of LC50s for copper of fresh water species. . . . . . . . . . 2-3
4-2
Fathead minnow growth tests for STP, refinery and chemical
effluents, Lima, Ohio, 1982. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4-2
Comparison of fathead minnow weights in refinery effluent
using two dilution waters, Lima, Ohio, 1982 . . . . . . . . . . . . . . . . . 4-3
Ceriodaphnia young production in three effluents, Lima, Ohio,
1982 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 4-4
Ceriodaphnia young production in ambient stream stations,
Lima, Ohio, 1982 ..................................... 4-6
4-3
4-4
5-1
Fathead minnow growth tests for STP, refinery, and chemical
effluents, Lima, Ohio, 1983. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5-2
Fathead minnow growth tests for ambient stations, Lima,
Ohio, 1983 .......... . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5-4
Ceriodaphnia young production in three effluents,
Lima, Ohio, 1983 ..................................... 5-4
Ceriodaphnia young production for ambient stations,
Lima, Ohio, 1983 ..................................... 5-5
5-2
5-3
5-4
6-1
Surface dilution contours in the Ottawa River
downstream from the STP, 21 September 1982 .............. 6-2
Bottom dilution contours in the Ottawa River
downstream from the STP, 21 Sept~mber 1982 .............. 6-2
Dilution contours in the Ottawa River downstream from the
refinery, 23 September 1982 ............................ 6-4
Dilution contours in the Ottawa River downstream from the
chemical plant, 25 September 1982 ................. . . . . . . 6-5
Effluent contribution to receiving water. . . . . . . . . . . . . . . . . . . . . 6-6
Spatial distribution of periphyton community indices and
associated parameters, 1982 survey....................... 7-2
Spatial distribution of key periphyton taxa, 1982 survey. . . . . . . . 7-4
6-2
6-3
6-4
6-5
7-1
7-2
8-1
Spatial patterns of benthic species diversity and
components of diversity, Ottawa River, 1982 survey. . . . . . . . . . . 8-3
Spatial abundance patterns of key benthic taxa, Ottawa
River, 1982 survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8-4
Spatial abundance patterns of the dominant ephemeropterans,
Ottawa River, 1982 survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8-5
Spatial distribution of major benthic groups, 1982 survey. . . . . . . 8-6
Spatial trends of proportion of population in drift compared to
benthic standing crop for major taxonomic groups,
1982 survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 8-7
8-2
8-3
8-4
8-5
x
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Figure
10-1
11 -1
11-2
12-1
13-1
14-1
14-2
14-3
14-4
A-1
List of Figures (Continued)
Page
9-1
Spatial distribution of fish community indices and associated
parameters, 1982 survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9-3
Spatial distribution of selected fish species and community
parameters, 1982 survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9-4
9-2
Results of in situ fish caging study, Ottawa River,
1982 survey. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 10-2
Spatial trends of benthic community parameters, 1983. . . . . . . . 11-1
Spatial trend of major benthic taxonomic groups, 1983 . . . . . . . . 11-2
Spatial trends of selected fish abundances. July 1983 ........ 12-2
Spatial trends of zooplankton components of the plankton.
July 1983 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 13-2
Correlation of Ceriodaphnia young per female with benthic
parameters from eight stations in the Ottawa River, Lima.
Ohio, 1982 .... . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-3
Correlation of Ceriodaphnia young per female and algal
diversity at eight stations in the Ottawa River, Lima. Ohio,
1982 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-3
Ambient toxicity correlation between Ceriodaphnia
young per female and ecological survey data for 1982
Ambient toxicity correlation between Ceriodaphnia
young per female and ecological survey data for 1983
. . . . . . . . 14-3
. . . . . . . . 14-4
Test chamber for static renewal fathead minnow larvae
growth test. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . A-2
XI
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Foreword
This report is the first in a series of reports which present the results of the
Complex Effluent Toxicity Testing Program. The program is a multi-year research
project conducted by EPA's Environmental Research Laboratory, Duluth,
Minnesota, and the Permits Division, Office of Water Enforcement and Permits,
Washington, DC. Contractor support was provided by Ecological Analysts, Inc. of
Baltimore, Maryland.
The Complex Effluent Toxicity Testing Program was initiated to support the
developing trend toward water quality-based toxics control in the National
Pollutant Discharge Elimination System (NPDES) permit program. It is designed
to investigate, under actual discharge situations, the appropriateness and utility
of "whole effluent" toxicity testing In the identification, analysis, and control of
adverse water quality impact caused by the discharge of toxic effluents.
Until recently, the focus of NPDES permitting was on achieving technology-
based control levels for toxic and conventional pollutants. Regulatory authorities
set permit limits on the basIs of national guidelines. Control levels reflected the
best treatment technology available considering technical and economic
achievability. Such limits did not, nor were they designed to, protect water
quality on a site-specific basis.
The NPDES permits program, in existence for over 10 years, has achieved the
goal of the implementation of technology-based controls. With these controls
largely in place, future controls for toxic pollutants will, of necessity, be based on
site-specific water quality considerations. Unfortunately, there has been less
practical experience in setting water quality-based controls, particularly for
toxicants, than in setting technology-based controls.
Setting water quality-based controls for toxicants can be accomplished in two
ways. The first is the pollutant-specific approach which involves setting limits for
single chemicals based on laboratory derived no-effect levels. The second is the
"whole effluent" approach which involves setting limits using effluent toxicity
as a control parameter. There are advantages and disadvantages to both
approaches.
The major advantages of the pollutant-specific approach include the capability to
design treatment for specific chemicals in an effluent and the availability of large
amounts of data on the effects of some individual toxicants. Although these data
are available for only a small number of toxicants, the regulatory authorities are
familiar with it and use it extensively. The disadvantages of the approach are that
it cannot cover the large number of potentially toxic pollutants in wastestreams,
the effects of mixtures cannot be determined, and the bioavailability of individual
chemicals at different discharge sites cannot be ascertained. For the whole
effluent approach, the major advantages include the capacity to analyze the
combined toxicity of all constituents of complex effluents and the ability to
measure the bioavailability of those constituents. The major disadvantages are
that there is a lack of toxicity treatability data and permitting experience.
Regulatory authorities are unfamiliar with this approach.
Effluent toxicity has not been used as an effluent control parameter in NPDES
permitting despite its practicality potential. Even many water quality specialists
XII
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have been hesitant to employ toxicity as a control parameter. There are two
reasons which can be identified. First. toxicity tests have been considered too
imprecise and too variable to be used in controlling toxics in permits. Second,
there is no effluent toxicity database available to indicate what measured
effluent toxicity really means in terms of receiving water impact. There has been
considerable criticism directed at toxicity testing as a permitting tool because it
was thought that the results of effluent toxicity testing did not translate to
instream biological impact.
The Complex Effluent Toxicity Testing Program has been designed to analyze
these concerns. The program has four major purposes:
1. To investigate the validity of effluent toxicity tests to predict and quantify
adverse impact to receiving waters caused by the discharge of toxic
industrial and municipal effluents;
2. To determine appropriate testing procedures which will support regulatory
agencies as they begin to establish water quality-based toxics control
programs;
3. To serve as practical case examples of how such testing procedures can be
applied in different toxic effluent discharge situations involving single and
multiple discharges in a variety of dilution situations; and
4. To field test recently developed short-term chronic toxicity tests involving
the test organisms Ceriodaphnia and Pimephales promelas.
Study sites were selected on the basis of several selection criteria. The primary
criterion was that the receiving water had to have a history of adverse water
quality impact which was associated with existing NPDES discharges. Other
selection criteria included relatively low available dilution at low flow periods,
the presence of a mix of industrial and municipal dischargers, the probability of
the discharges containing toxic pollutants at toxic levels, and the cooperation of
both the regulatory agencies and the regulated community.
To date, six sites have been investigated involving 11 municipal discharges and
about 30 industrial discharges. They are, in order of investigation:
1. Ottawa River, Lima, Ohio
2. Scippo Creek (tributary to the Scioto River), Circleville, Ohio
3. Five Mile Creek, Birmingham, Alabama
4. Skeleton Creek, Enid, Oklahoma
5. Naugatuck River, Waterbury, Connecticut
6. Patapsco and Back Rivers, Baltimore, Maryland
The Lima, Ohio site and the Birmingham, Alabama site were subjected to further
analysis for comparative purposes one year after the initial site visits were
conducted. Two more sites involving larger rivers and estuaries are planned for
study during 1984.
This project is a research effort only and has not involved either NPDES permit
issuance or enforcement activities. Toxicity testing of the effluents was
conducted for research purposes only.
The following report describes the Lima, Ohio study conducted in September
1982 and July 1983.
Rick Brandes
Permits Division
Nelson Thomas
ERL/Duluth
Project Officers
Complex Effluent Toxicity
Testing Program
xiii
-------
Executive Summary
EPA recently issued a policy which provides for control of the discharge of toxic
substances through the use of numerical criteria and effluent toxicity limits in
NPDES permits. This is the first broad scale effort to use effluent toxicity in the
NPDES permit program and a scientific basis for this approach is needed.
The research on the Ottawa River described in this report had three objectives:
1. Determination of effluent and ambient stream toxicity to Cer;odaphn;a,
fathead minnows, and indigenous species.
2. Definition of the response of the biological community to point-source
discharges.
3. Evaluation of the effectiveness of toxicity testing techniques in predicting
ambient toxicity to indigenous communities.
The Ottawa River at Lima, Ohio receives discharges from the municipal sewage
treatment plant (STP), a refinery, and a chemical company. In addition to the
three effluents, toxicity tests were conducted on samples from 13 river stations.
Biological studies were conducted at eight of the stations and included benthos,
fish, algae, and zooplankton. Studies were conducted in 1982 and 1983 to
assess the reproducibility of methodologies and results.
The STP effluent was toxic to Cer;odaphn;a but not to fish. The river downstream
from the STP was toxic and there was a severe biological impact in that same
area. The refinery effluent was tOXIC to both test organisms. The river was also
toxic downstream from both the refinery and the chemical plant. Both the
benthic and fish communities were severely altered in these areas. The
biological impact ended at the same stations as those having no toxicity in the lab
tests.
Based on toxicity measurement of effluents and river water, toxicity tests did
predict the resulting toxicity downstream from the discharges. A correlation was
established between ambient toxicity, effluent toxicity and biological impact
which suggests that effluent and ambient toxicity tests are accurate predictors of
receiving water impact.
XIV
-------
Quality Assurance
Coordination of the various studies was completed by the principal investigator
preceding and during the onsite work. A reconnaissance trip was made to the
site before the study and necessary details regarding transfer of samples,
specific sampling sites, dates of collections, and measurements to be made on
each sample were delineated. The evening before the study began, a meeting
was held onsite to clarify again specific responsibilities and make last minute
adjustments in schedules and measurements. The mobile laboratory was
established as the center for resolution of problems and adjustment of work
schedules as delays or weather affected the completion of the study plans. The
principal investigator was responsible for all Quality Assurance related decisions
onsite.
All instruments were calibrated by the methods provided by the manufacturers.
For sampling and toxicity testing, the protocols described in the referenced
published reports were followed. Where identical measurements were made in
the field and laboratory, both instruments were cross-calibrated for consistency.
xv
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,.
Introduction
To date. the focus of water pollution control in the
National Pollutant Discharge Elimination System
(NPDES) permits program has been on the attainment
of national technology requirements and the imple-
mentation of water quality criteria for the 129
"priority pollutants." However, implementation of
these standards and criteria does not always guar-
antee that certain dischargers will not cause adverse
effects to receiving waters. Industrial and municipal
effluents often contain large numbers of potentially
toxic pollutants which can move through treatment
systems virtually untreated. Often these are pollut-
ants for which little or no toxicity data exist. Further
complications arise from the potential interaction of
combinations of pollutants to increase or decrease
toxicity.
Future activities in water pollution control will focus
on the control of toxic pollutants which impact water
quality. There are two methods used in controlling
toxic impact: pollutant-specific controls and "whole
effluent" toxicity-based controls. Because toxicity
testing evaluates a living organism's response, it has
an advantage over chemical-specific analyses which
may not identify all pollutants in a wastewater sample
and which cannot detect toxicity interactions. Toxicity
information can indicate the need for additional
characterization of an effluent and can also provide a
basis for permit limits based on state water quality
standards for toxicity- or technology-based require-
ments.
The primary purpose of this study is to investigate the
relationship between effluent toxicity data and eco-
logical response. Thus. three objectives must be met:
1. Determination of effluent and ambient stream
toxicity to Ceriodaphnia, 8 fathead mi n nows, and
indigenous species.
2. Definition of the response of the ecological
community to point-source dischargers.
3. Evaluation of the effectiveness of toxicity testing
techniques in predicting ambient toxicity to
indigenous communities.
"The species used In the 1982 study was Ceflodaphnia retlculata The
species of Ceriodaphnia used for these tests is not known with certainty
The stocks were thought to be C. reticulata but. in November 1983. based on
taxonomic verification by Dorothy Berner. Ph.D. (Temple University. PAl. a
second species. C. affinis/dubia. was also discovered In the stock cultures
The exact determination of the species tested IS not critical to this study. and
all reference IS to the genus only In this report
This report is organized into sections corresponding
to the project tasks. Following an overview of the
study design and a summary of the description of the
site. the chapters are arranged into toxicity testing.
hydrology, and ecological surveys for the two study
periods (September 1982 and July 1983). An integra-
tion of the laboratory and field studies is presented In
Chapter 14. All methods and support data are
included in the appendixes for reference.
1 -1
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2.
Study Design
The primary purpose of this study was to investigate
the ability of laboratory effluent toxicity tests to
predict ambient stream toxicity impacts at a multiple
discharge site on a small river system. The site
chosen for study was the Ottawa River near Lima,
Ohio. The study area included three dischargers: a
sewage treatment plant (STP), a refinery, and a
chemical plant. A more complete description of the
study area is found in Chapter 3. This study required
laboratory tests that centered on expected effluent
dilution concentrations and organisms that had
toxicity sensitivitiy similar to indigenous stream
organisms. In conjunction with these toxicity tests,
ecological surveys of the Ottawa River were con-
ducted to identify structural effects to representative
biotic communities and selected populations from
point source discharges. Hydrological analyses in-
cluded effluent configuration studies to define the
mixing and interactive characteristics of the effluents.
The results from all of these study components were
then compared. Thus, the study of the Ottawa River
(Figure 2-1) at Lima, Ohio, consisted of four parts:
1. Effluent and ambient toxicity testing using the
7-day Ceriodaphnia. fathead minnow, and indig-
enous species test,
2. Biological community characterization,
3. Hydrological measurements, and
4. Integration and interpretation of results.
The study was conducted initially during 21-28
September 1982. A follow-up study was conducted
7-8 July 1983 following an operational modification
by the refinery. The methods used in the study during
the two time periods are detailed in Appendixes A, B,
and C. The respective study designs for the laboratory
and field aspects as well as the data analysis task are
outlined in the following sections.
2.1 Toxicity Testing Study Design
Toxicity tests were performed on each of the three
effluents to measure subchronic effects on growth of
larval fathead minnows and chronic reproductive
effects on Ceriodaphnia. A range of effluent concen-
trations was used so that acute mortality also could
be measured, if it existed. Acute toxicity is defined as
short-term effects with lethality as the endpoint.
Chronic toxicity is considered long term (length of
time is dependent upon test species). where both
lethal and sublethal effects are considered. For these
tests, acute mortality is usually measured at 48 hours
for Ceriodaphnia and 96 hours for fathead minnows.
The objective of these tests therefore was to estimate
the minimum concentration of each effluent that
would cause acute mortality and chronic effects on
growth (fathead minnows) or reproduction (Cerio-
daphnia).
Resident species from eight different families were
also,tested for acute toxicity of each effluent. This was
done to determine if there were any species more or
less resistant to the effluents than the fathead
minnows and Ceriodaphnia used in the chronic tests.
However, many problems inherent in testing indig-
enous species resulted, giving invalid test results.
Therefore, these data are not presented.
In 1982, the dilution water for the effluent tests was
taken from immediately upstream of each discharge.
Therefore, the second discharge downstream of the
first was diluted with stream water containing a
portion of the upstream effluent, and the most down-
stream effluent of the three discharges was diluted
with stream water containing some of both upstream
effluents (see Figure 2-1). Thus, the inherent toxicity
of the two downstream discharges was not measured
but rather the combined effects of that effluent and
the upstream effluent(s). This approach was neces-
sary because the objective was to estimate impact
below each discharge.
A separate set of tests was performed with both
Ceriodaphnia and fathead minnows on the refinery
effluent in which a high quality dilution water (Lake
Superior water) was used in order to measure only
the inherent toxicity of the refinery waste. Another
Ceriodaphnia test was conducted using unchlorinated
STP effluent and diluent water from above the City of
Lima. The purpose of this test was to determine if any
toxicity observed was due to chlorination or contribu-
tions from runoff from the City of Lima.
In addition to the above tests (hereafter referred to as
the effluent dilution [ED] tests). stream stations were
established from above the discharges extending
downstream to just before the confluence with the
Auglaize River to measure ambient toxicity. The
purpose of these tests was to measure the loss of
toxicity of the effluents after mixing, dilution from
other stream inputs, degradation, and other losses
such as sorbtion. The tests would also provide data for
2-1
-------
Figure 2-1. Study eree. Ottawe River. lime. Ohio.
~
p'"mb"' G,,"
Sampling
Sites
River
Distance (kml
Station 1
Station 2
Station 3
Station 3A
Station 3B
Station 4
Station 4A
Station 5
Station 6
Station 7
Station B
Station BA
Station 9
RK 740
RK 60 7
RK 60 3
RK 60 2
RK 59 7
RK 594
RK 5B 4
RK 57 1
RK 52 5
RK 46 3
RK 25 7
RK 129
RK 16
~og I Creek
Llltle HOg: Ada n
00 V
Creek UI U
Lafayette ~1 ~ q,~
- c}
~I ~ ,,"
I cl'
,
"
" ""
5 "...
"' "' "
" ""'
" ' "
" " "
" " "' STP
,,'
"
" ~ - Refinery
"
~ - Chemical Plant
Miles
0 1 2 3 4 5
Kilometers
.
0 2 4 6 B
prediction of ecological impact for comparison with
the stream biological survey. Only Ceriodaphnia were
used in the ambient toxicity test.
In the 1983 testing, each effluent was diluted with
water collected above all known point source dis-
charges because it was considered to be of good
quality. This contrasts with the 1982 work in which
diluent water came from upstream of each outfall.
Also. unchlorinated STP effluent was not tested.
Ambient stream toxicity tests were also performed in
1983; however, they included both Ceriodaphnia and
fathead minnow larvae.
2.2 Field Survey Study Design
The study components of the 1982 field survey
included quantitative assessment of the periphytic,
2-2
benthic macroinvertebrate. and fish communities
and a fish caging study. Nighttime drift samples at
selected transects were collected to examine dis-
persal characteristics of the benthos and population
structure of the macrozooplankton community.
The periphyton study investigated effects and recov-
ery of the periphytic community by measuring
chlorophyll a and biomass and by estimating compo-
sition and relative abundance. The relatively short
reproduction time and rapid seasonal fluctuation in
growth of periphytic algae make that community a
useful indicator of localized effects resulting from
effluent toxicity.
The benthic survey investigated ambient community
response to the effluent(s) and approximated the
-------
location of downstream recovery should effluent
discharge effects be substantiated. The benthic
community is considered a good indicator of ambient
response to adverse conditions because of its general
lack of extensive mobility. The degree of community
stability within affected areas can be measured by
comparing composition and dominance to that of
non affected areas.
In addition to benthic collections, drift collections
were taken to evaluate the extent of colonizing
potential from the source population, to measure the
populations' response to plume entrainment, and to
assess the resiliency of the drift dispersal mechanism
immediately below the area of estimated influence.
The fisheries survey investigated the fish community
to discern any changes in composition and dominance
from previous surveys and to evaluate the response to
the respective effluents.
In conjunction with the fisheries surveys, in situ fish
caging surveys were performed to investigate in situ
response to toxicity of resident fish species.
A hydrological analysis was conducted which con-
sisted primarily of a dye study performed at each of
three sites to identify the individual dilution charac-
teristics of each effluent. By modeling downstream
dilution contours for each discharger, the exposure
concentration pertinent to instream effects could
then be quantified. Ancillary flow measurements
were also taken to estimate the flow contribution of
the discharges to the receiving waterbody.
In the 1983 effort, a 2-day field survey was conducted
in which the zooplankton, benthos, and fish were
sampled at most of the same stations as in 1982. No
hydrologic work was done during the 1983 survey.
2.3
Approach to Integretation 01
Laboratory and Field Efforts
Laboratory toxicity tests were conducted to measure
the no-effect concentrations of three effluents. The
toxicity of receiving water was also measured at
various stream stations to confirm that the concentra-
tions of effluents found to have effects in toxicity tests
were similar to receiving water effluent concentra-
tions that caused toxicity in the receiving stream.
These data can then be compared to measures of the
stream community data to validate or refute impacts
predicted by the laboratory tests. If predictions were
valid, then the effluent dilution test data could be
used to estimate how much toxicity reduction would
be necessary to diminish the impact.
Species sensitivity is one of the major problems in
attempting to relate single species toxicity tests to
impacted biological communites. One must have a
degree of confidence that the test species is as
sensitive as most of the community it is protecting. As
an example, Figure 2-2 illustrates the results of
copper LC50's for a number of species of freshwater
organisms. Some species are sensitive at very low
concentrations while other species survive concen-
trations that are several orders of magnitude higher.
It is important to test a number of organisms to find a
range of response levels in different discharge situa-
tions that, together, adequately predict instream
community response. The purpose of measuring this
range is to find the lowest end of the range of
sensitivities, i.e., to find the more sensitive individual
species. Toxicity to this species will represent the
"worst-case" exposure conditions which will occur.
Testing with a vertebrate (fish) and an invertebrate
(Ceriodaphnia) provides a measure of toxicity that is
not achieved by studying only one type of organism.
Figure 2-2. Histogram of LC50s for copper of fresh water
species.
10
9
~ 8
.~ 7
~'6
'0 5
... 4
Q)
.Q 3
~ 2
z 1
..... ...
.. ............
....... ... .
-1
o
2
1
Log of LC50
3
There is a high probability that the sensitivity of the
species tested in chronic toxicity tests falls within the
range of sensitivity of the species in the receiving
stream, but usually the position of the species within
the range is unknown. The sensitivity of the species
tested will change depending on the types of toxi-
cants.
The measures used in the toxicity tests, i.e., growth,
reproduction, and mortality, are not the same meas-
ures of impact used for the biological assessment of
the communities. As discussed above, the basic
assumption is that the tested species are within the
sensitivity range of the community, but it is not known
where in that range they fall; therefore, the best way
to compare 1he field and laboratory data would be to
use measures of community response that include all
species. If all species are included, then it does not
matter whether the test species are in the most
sensitive or least sensitive end of the range because
some or many species in the community should show
impact at the same or lower effluent concentrations.
The response would be that their populations would
be reduced in numbers from reference populations. If
the affected species happen to be at lower trophic
levels, there may also be impacts on other species
which are not directly affected by toxicity, but are
indirectly affected by alteration of the food chain.
2-3
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3.
Site Description
Several publicly owned treatment works (POTWs)
and privately owned industries discharge treated
effluents to the Ottawa River (Figure 2-1). The
principle dischargers to which this study was directed
are a sewage treatment plant (STP), a refinery, and a
chemical company. The STP contributes the largest
volume with a nominal flowofO.53 m3/sec (12 mgd),
accounting for approximately 83 percent of the
Ottawa River flow during the study period. As of the
study period, the refinery discharges an average of
0.24 m3/sec (5.5 mgd) and the chemical plant
discharges about 0.088 m3/sec (2.0 mgd).
The most upstream discharge is the STP. It is an
activated sludge plant with ammonia removal and
chlorination to provide a residual of 0.1-0.2 mg/liter
of total chlorine. The plant appeared to be well
operated and treatment efficiency was extremely
good.
The next discharge is from a refinery located approx-
imately 0.8 km downstream from the STP The
treatment plant had consisted of aerated lagoons
with an approximate 15-day retention time during the
1982 study. Additional treatment was being brought
online at the time of the 1983 study. This plant also
treats wastewater from the agricultural chemical
division of an adjacent chemical plant.
The third discharge is from a chemical plant. That
discharge contained only cooling water at the time of
the 1982 study because the industrial chemicals
division was closed and the waste from the agricultural
chemical division went to the refinery treatment
plant. The industrial chemical division had been
closed since the September 1982 study but when it
was operating, ammonia was one of the main
components ofthe waste. In 1983, a dry ice operation
had been added and the effluent also contained
discharge from the new agriculture section.
The study area on the Ottawa River in northwestern
Ohio extended from Lima to Kalida, Ohio. It incor-
porated nearly 72 river kilometers (RK), 9 biological
sampling locations, and 13 stations for ambient
toxicity tests. The Ottawa River is about 15-20 m wide
and has depths varying from 0.3 m in riffle areas to
1.5-2 m in pool areas. The primary habitat type is
pools with infrequent riffle areas.
The station descriptions and approximate locations
depicted in Figure 2-1 are:
1. Reference transect (RK 74.0) located above any
influence from Lima at Thayer Road bridge.
2. Reference transect (RK 60.7) about 0.2 km
above the STP, but downstream from other
discharge points in the City of Lima.
3. Transect (RK 60.3) about 0.3 km below the
discharge of the STP
3a. Transect (RK 60.2) about 0.5 km below the
discharge of the STP
3b. Transect (RK 59.7) about 0.2 km above the
refinery discharge.
4. Transect (RK 59.4) about 0.5 km below the
discharge of the refinery.
4a. Transect (RK 58.4) 0.8 km below the chemical
plant discharge.
5. Transect (RK 57.1) at Shawnee Road bridge 2.1
km below the discharge of the chemical plant.
6. Transect (RK 52.5) at Rt. 117 bridge just above
the Shawnee STP
7. Transect (RK 46.3) at Allentown Road bridge
just below Shawnee STP and Allentown Dam.
8. Transect (RK 25.7) at Rimer at Rt. 198.
8a. Transect (RK 12.9) between Rimer and Kalida.
9. Transect (RK 1.6) below Kalida prior to the
confluence with the Auglaize River.
All of the above stations were used for ambient water
collections for the toxicity testing in 1982. Biological
collections were made in 1982 at the above stations
with the exception of those labeled "a" or "b."
Stations 2, 3, 4,5,6,7, and 8 were sampled in 1983
for the biological survey and ambient water collec-
tions.
Water temperature, dissolved oxygen (DO), specific
conductance, and pH were measured during bio-
logical collections at each station in 1982. A Hydrolab
Model 4041 was used for all measurements.
Water temperature ranged from 13.3 to 20.0oC
during the study week in September 1982. The
highest temperature occurred at stations near the
plant outfalls (Stations 2 through 6). Conductivity
ranged from 983 to 1,593 jJmhos/cm. Discharges
from the City of Lima, the refinery, and the chemical
company all appeared to increase the conductivity,
whereas the STP discharge decreased it. The pH
3-1
-------
values ranged from 6.2 to 8.4 throughout the study
area.
Dissolved oxygen ranged from 3.4 mg/liter (35
percent saturation) at Station 7 to 15.9 mg/liter
(greater than 150 percent saturation) at Station 8.
Supersaturated conditions were found at the STP and
refi nery discharge stations, but these dropped to
lower levels at the next three stations. DO measure-
ments at Station 8 (taken at mid-afternoon), however,
approached supersaturated levels. Although diel DO
measurements were not made during this study,
comparison between levels recorded at different
times of day over the study period indicate that daily
fluctuation at some stations was great. This was most
pronounced at Stations 2, 5, and 7. However, DO
levels equaling 75 percent saturation were recorded
at the reference station (Station 2) at 0930 hours on
21 September and at 1800 hours on 24 September,
indicating more stable water quality above the
influence of the three discharges.
Stream flow was very low during both sample
collection periods (September 1982 and July 1983).
The flow prior to the STP discharge (station 2) was
measured to beO.11 mJ/sec in September 1982. The
total flow at Kalida (Station 9) during the 1982 survey
was estimated to be 1.08 mJ/sec.
3-2
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4.
Toxicity of Effluents and Receiving Water, 1982
Toxicity tests were performed on each of the three
effluents to measure subchronic effects on growth of
larval fathead minnows and chronic reproductive
effects on Ceriodaphnia. A range of effluent concen-
trations were used so acute mortality (if it existed)
could be measured in addition to chronic toxicity.
The objective was to estimate the minimum concen-
tration of each effluent that would cause acute
mortality and chronic effects on growth (fathead
minnows) or reproduction (Ceriodaphnia). These
effect levels would then be compared to the effluent
concentrations in the Ottawa River to predict where
impact on resident species should occur. The validity
of these predictions could be determined by an
examination of the biotic condition of the stream at
the locations where such effluent concentrations
occurred as determined by the simultaneous stream
biological survey and hydrological studies. The meth-
ods used for toxicity testing are described in Appendix
A and follow those developed by Mount and Norberg
(1984) and Norberg and Mount (in press).
4.1 Chemical! Physical Conditions
Temperatures were maintained between 22 and
25°C for the duration of the tests. The mobile
laboratory did not have precise temperature control,
but diel temperature changes were gradual and
posed no problem.
The water hardness varied from 350 to 550 mg/liter
as CaC03, depending on river station and effluent
concentration. Alkalinity varied from 250 to 300
mg/liter. Only Station 1 had a hardness over 450
mg/liter. There were limestone quarries operating
near Station 1 and dust from the operation may have
caused a local increase in hardness. There were no
surface streams draining from the quarries during the
period of study.
Dissolved oxygen (DO) (mg/liter) was measured
frequently because these were renewal tests and
high biochemical oxygen demand (BOD) levels could
cause DO to be depressed. The sewage treatment
plant (STP) effluent had almost no measurable BOD,
and, because the chemical plant effluent was all
cooling water, BOD was probably similar. DO concen-
trations in the refinery waste were high during
daylight hours as a result of dense alQal populations.
At night in the test chamber, especially in the fathead
minnow tests, DO dropped markedly, due perhaps to
a combination of algal respiration and BOD from
bacterial action.
Initial DOs (when tests were set up) for the Cerio.
daphnia tests ranged from 7.5 to 8.4 except for the
ambient test Stations 4 through 7 where, on cloudy
days, they ranged from 4.5 to 5.0. Final DO values
(taken just before test solutions were changed) for the
Ceriodaphnia tests were all above 5.0 except for two
measurements (3.8 and 4.0) in the refinery test and
two measurements (41 and 4.9) at Stations 6 and 7 In
the ambient test. A total of 80 percent of DO readings
were above 6.0 mg/liter.
Initial DOs for the fathead minnow tests were the
same as for the Ceriodaphnia tests. After the first
24-hour period, DO ranged from 3.1 to 4.5 mg/liter
Upon discovery of this condition, feeding level was
reduced and extra care exercised in siphoning the
dead brine shrimp. Final values subsequently were
above 5.0 mg/iiter with several exceptions down to
4.0 mg/iiter in the refinery effluent dilutions
River pH varied depending on sunshine and time of
day. In the tests, pH usually ranged from 8.0 to 82,
both initial and final. The pH changed little during the
24-hour period of exposure to each sample. Inorganic
suspended solids in the stream were very low because
there was no runoff. The water color was greenish
from algal blooms occurring In the pools above the
dams in the City of Lima.
4.2 Results of Fathead Minnow
Growth Test
Results of the testing of fathead minnow larvae
exposed to various concentrations of the three
effluents indicated that the STP had no effect on
survival at any concentration (Table 4-1) The refinery
waste caused substantial mortality at 50 percent
effluent (Table 4-1, Figure 4-1) and a statistically
significant (P - 0.05) amount of mortality at 10
percent effluent. The chemical plant waste was not
toxic at 100 percent concentration, but toxicity was
observed at the lower concentrations and also In the
dilution water as shown by the low control survlval8
'Because the water used for controls and effluent dilution exhibited tOXiCity
a direct evaluation 01 the tOXiCity of the chemical plan! IS not possible
4-1
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Table 4-1. Seven-Day Percent Survival of Larval Fathead
Minnows Exposed to Various Concentrations of
Three Effluents in Upstream Water. Lima, Ohio,
1982 % Effluent (v/v)
Effluent by
Replicate 100 50 10 5 Control
STP
A 100 90 100 100 80 100
B 100 100 90 100 100 90
C 100 100 100 100 80 100
o 100 100 100 90 100 100
Mean 100 97.5 97.5 97.5 90 97.5
Refinery
A 0 20 70 80 100 90
B 0 30 80 100 90 90
C 0 0 80 80 100 100
o 0 0 70 100 100 100
Mean 0 12.5 75 90 97.5 95
Chemical Plant
A 80 70 40 40 50 40"
B 90 70 40 20 50 20
C 100 80 50 40 60 40
o 90 60 40 36.4 50 20
Mean 90 70 45 34.1 52.5 33.3
"Controls reflect presence of refinery waste as do the lower
effluent concentrations of the chemical plant.
(Table 4-1). Based on the results of the hydrological
measurements taken concurrently, the dilution water
for the chemical plant discharge (taken below the
refinery discharge point) was approximately 29
percent refinery waste (Table 4-2), which is a con-
centration high enough to account for the mortality
observed in the chemical plant waste control and the
1. 5, and 10 percent concentrations. The 10 percent
chemical plant waste dilution was estimated to be 24
percent refinery waste.
The final fathead minnow weights after 7 days'
exposure to the three effluents diluted with upstream
water crre given in Table 4-3 and Figure 4-1. The
relative toxicity as based on growth is essentially
identical to the effect on mortality indicating that the
toxicity of the refinery waste on fathead minnow
growth occurred at about 10 percent effluent concen-
tration. This toxicity of the refinery affected the
results of the growth test performed on the chemical
plant effluent.
Two dilution waters (Lake Superior and the receiving
water) were used in testing concentrations of the
Average Concentration (%) of Stream Water and
Effluent Below Each Discharge During the 1982
Testing Period"
Concentration of Effluent (%)
Chemical Stream
Location STP Refinery Plant Water
Below STP 77 0 0 23.0
Below refinery 57.7 28.8 0 13.5
Below chemical plant 52.5 26.9 9 11.6
"Based on hydrological measurements expanded in Table 6-3.
Table 4-2.
4-2
Figure 4-1. Fathead minnow growth tests for STP, refinery and
chemical effluents, Lima, Ohio, 1982.
100
---- u---------------- ------"""
'\
\
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\
\
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.
.\
. \
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\
,
,
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,
,
80
01
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.;;;
5 60
(/)
Percent Survival
- = STP Effluent
-U_n- = Refinery Effluent
. ... = Chemical Effluent
20
o
10
100
Growth (dry weight)
- - STP Effluent
---_u - Refinery Effluent
............. = Chemical Effluent
- 0.6
C>
I
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o
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01
~ 0.2
- - - - - - --- - -- - ---- - -- -- -", "-
....
,
...., ....., ............, "'<"
,
,
'-,
,
,
,
,
o
10
Percent Effluent (vol/vol)
100
refinery effluent in a side-by-side comparison to
ascertain the inherent toxicity of the refinery waste
(Table 4-4). However, fathead minnow growth was
similar in the two dilution waters with slightly higher
weights attained in the refinery waste concentrations
using the Lake Superior dilution water (Table 4-5,
Figure 4-2). No statistical analysis was performed to
test this difference.
4.3 Results of Reproductive Potential
Tests Using Ceriodaphnia
The young production of Ceriodaphnia in various
effluents diluted with stream water immediately
upstream from each outfall was the primary focus of
the reproductive potential tests. The mean young/
female is calculated as the total young produced in 7
days at each concentration divided by the original
number (10) of animals used. Therefore, early mortal-
ity of the original animals will reduce the young per
-------
Table 4.3.
Table 4.6.
Mean Dry Weight (mg) of larval Fathead Minnows
Exposed to Refinery Effluents Diluted with Two
Different Dilution Waters. lima. Ohio. 1982
Mean Dry Weight (mg) of larval Fathead Minnows
Exposed to Three Effluents at Various Concentra.
tions. lima. Ohio. 1982
% Effluent (v v)
Effluent by
Replicate 100 50 10 5 Control
STP
A 032 046 057 047 052 041
8 032 051 054 052 042 037
C 0.36 040 051 056 049 045
D 035 047 051 045 043 029
Mean 034 0.46 053 050 046 038
SD 002 004 003 005 005 007
Refinery
A 006 039 040 042 031
8 018 036 042 043 036
C 028 037 046 030
D 029 042 037 041
Mean 012 033 040 042 034
SD 009 005 002 004 005
Chemical Plant
A 043 029 033 019 026 023.
8 039 035 023 030 019 013
C 036 036 028 025 009 022
D 058 0.30 020 028 014 025
Mean 044 0.32 026 026 017 021
SD 010 004 006 005 007 006
.Controls for chemical plant were affected by tOXICity of refinery
waste
female regardless of how rapid young production of
surviving adults may be. The percent survival of the
test organisms was also compared among test
concentrations to measure lethality.
The 100 and 50 percent chlorinated STP effluent
caused mortality in 2-5 days (Table 4-6). The mortal-
ities in the 10. 5. and 1 percent concentrations and
controls were thought to be ca used by the occurrence
of a toxic slug of water from upstream. as described
later in this section. The existence of a toxic slug of
water from an upstream source is hypothesized on
the basis of mortality of control organisms and test
Table 4.4.
Seven-Day Percent Survivel of larval Fathead
Minnows Exposed to Refinery Waste Diluted
with Two Different Dilution Waters. lima. Ohio.
1982
% Effluent (v/v)
Replicate 100. 50 10 5 Control
Receiving Water"
A 0 20 70 80 100 90
8 0 30 80 100 90 90
C 0 0 80 80 100 100
D 0 0 70 100 100 100
Mean 0 125 75 90 975 95
lake Superior Water
A 10 90 100 60 50
8 10 80 80 60 60
C 0 100 100 60 90
D 0 90 100 70 90
Mean 10 90 95 625 725
.100 percent effluent--no dilution water used; only four replicates
tested.
"DiJutlon water taken immediately upstream of the refinery
discharge.
00 Effluent (v vi
----- --
Replicate
Receiving Water"
A
8
C
D
Mean
SD
Lake Superior Water
A
8
C
D
Mean
SD
100.
Control
50
10
5
-_._~-_. -
006 039 040 042
o 18 0 36 0 42 0 43
o 28 0 37 0 46
n 029 042 037
o 1 2 0 33 0 40 0 42
o 09 0 05 0 02 0 04
031
036
030
040
034
005
o 24 0 32 0 38
o 10 045 0 41
o 40 0 42
041 041
017 040 040
o 10 0 05 0 07
o 40 0 34
042 0 49
o 35 0 40
031 038
o 37 040
o 05 0 06
--~-~----~
.100 percent effluentnno dilution water used. only four replicates
tested
"Dilution water taken Immediately upstream of the refinery
discharge
organisms not attributable to known effluents. Be-
cause of this mortality. the young per female is lower
than that which would have been obtained if they had
survived to 7 days.
The refinery waste was lethal at 100 percent and
nonlethal at 50 percent. The mortalities in 10.5. and
1 percent waste and control were due to the STP
effluent in the dilution water. The dilution water used
for the refinery waste was 77 percent STP effluent
(Table 4-2). In the 10 percent refinery concentration.
there was an approximate 69 percent concentration
of STP effluent-clearly enough to be lethal as
indicated from the STP test. Even at the 50 percent
refinery effluent concentration. there is 38 percent
STP effluent. which is probably toxic.
Figure 4.2. Comparison of fathead minnow weights in refinery
effluent using two dilution waters. lima. Ohio.
1982.
08~
-~- = River Water
. = L Superior Water
c;;
~ 06r-
.t:
C>
CI)
3: I
>04~-~-""--
j 02~%... "~
I
o
~~........_~ -
"-- _. - .-, ~- - ."--~
. ..
10
Percent Effluent (vol vol)
100
4-3
-------
Table 4-6.
Mean Young Per Original Female and Mean
Percent Survival of Adult C.riodephnie in Various
Effluent Concentrations Using Receiving Water
for Dilution, lima, Ohio, 1982
%
Effluent
(v/v)
Young/
Female
(X)
Days
3
SD
2
5
6
4
Percent Survival
CI2 STP Effluent
100 100 100 0 0 0 0 0
50 0.1 100 90 80 40 0 0 0
10 8.6 3.1 100 100 100 100 100 0 0
5 13.3 7.8 100 100 100 100 100 10 10
1 18.7 8.7 100 90 90 0 90 0 0
C 24.2 5.0 100 100 100 100 100 80 0
Refinery Effluent
100 0 90 0 0 0 0 0 0
50 3.2 2.8 100 90 90 90 90 90 90
10 3.5 4.2 100 100 100 100 0 0 0
5 1.7 1.9 100 100 100 80 0 0 0
1 0.4 100 100 80 30 0 0 0
C. 0 100 100 10 0 0 0 0
Chemical Plant Effluent
100 0.7 90 80 70 40 0 0 0
50 7.2 3.8 100 100 100 100 100 90 80
10 12.9 4.2 100 100 100 100 100 90 50
5 6.7 1.9 100 90 90 90 90 40 30
1 5.8 100 100 100 100 100 10 0
C. 3.3 100 100 100 100 90 40 10
UnCI2 STP Effluent
100 0 100 80 0 0 0 0 0
50 0.9 100 90 60 20 0 0 0
10 20.5 5.7 100 100 100 100 100 100 90
5 0 100 100 100 100 0 0 0
1 0.1 100 90 60 10 10 10 10
C 25.8 4.6 100 100 100 100 100 100 100
"Controls for the refinery effluent test reflect presence of STP
effluent, and in the chemical effluent test the combined toxicity of
STP and refinery is seen.
The chemical plant waste was lethal at 100 percent
(Table 4-6). The mortality at concentrations equal to
or less than 10 percent were caused by the toxic slug
of water mentioned previously. The dilution water
used for this test was about 58 percent STP effluent
and at 50 percent chemical waste concentration, the
STP effluent would have been at about a 29 percent
concentration which again is high enough to produce
mortality, except that the presence of about 14
percent refinery waste would have delayed the
mortality due to the STP effluent. The progressive
mortality and low young per female (7.2) on Days 6
and 7 at 50 percent chemical plant effluent may have
been caused by the STP effluent, the toxic slug, or
some combination of the two.
The interactive nature of the three effluents is illus-
trated in Figure 4-3 in which young production
increases in the refinery and chemical plant effluent
tests as concentration increases. or, conversely, as
volume of the STP effluent in the test water decreases.
However, young production also was reduced in 100
4-4
Figure 4-3. C.riodephnie young production in three effluents,
Lima, Ohio, 1982.
7
40 f
j30~
G;
Q.
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5 20
o
>
C
-------
might be attributable to runoff from the City of Lima.
The young per female and survival of the control
shows that Station 1 was acceptable. The very
regular pattern of mortality at 100,50, and 1 percent,
but not 10 percent, and the comparable effect on
young production does not seem likely due to chance,
sick animals, or contamination in the laboratory. The
mortality pattern in the 100 percent unchlorinated
effluent is nearly identical to that for the chlorinated
effluent so apparently the toxicant was not a product
of chlorination. The unchlorinated controls give no
evidence of the toxic slug shown by the chlorinated
waste controls.
One possible explanation for this unusual dose
response curve is that the toxicant was very pH-
dependent and was in a more toxic form at the pH of
these lower concentrations of waste. The effluent has
a pH from 7.2 to 7.4 and the control water was 8.3 or
higher. As the percent waste decreased, the pH
increased, approaching that of the control.s
The results of the ambient test for persistence of
toxicity are presented in Table 4-8 and Figure 4-4. At
Station 3, 3A, and 38, which contained 77 percent
STP effluent but no refinery waste, the mortality
started between Day 2 and 3 as would be predicted
from Table 4-6 and the test on chlorinated effluent.
Station 4 water contained 58 percent STP effluent
and 29 percent refinery waste. Mortality was delayed
by several days even though the drop in STP effluent
was only from 77 to 58 percent STP between Stations
38 and 4. The increase in mortality between Day 5
and 6 at Stations 38 and 4 coincides with the
mortality at Station 2 which had no STP or refinery
effluent. Note that at Station 6, which is almost 5 km
below Station 5, the increase in mortality was a day
later, occurring between Day 6 and Day 7. These
observations are well explained by the toxic slug
hypothesis mentioned earlier.
'Since this work was completed. similar toxicity has been observed in other
STP effluents.
The controls for the STP effluent dilution (ED) test on
chlorinated effluents showed a sharp rise in mortality
one day later than did the animals in the ambient test
at Station 2. Yet, the test water for both the controls
and the ambient Station 2 animals was taken from
the same 5-gallon sample, with the only difference
being that the sample sat overnight before being used
for the ED test. It could be speculated that the
difference was caused by the aging of the water used
for the ED test; however, the sudden mortality
increase in chlorinated STP concentrations of 1, 5,
and 10 percent occurred on the same day as for the
Station 2 animals. The sudden rise in mortality in the
controls and 1 and 5 percent concentrations of the
chemical plant ED test occurred also on the same day
as the mortality in the ambient test.
Since the mortality occurred on the same day in three
STP concentrations, in three concentrations in the
chemical plant ED test, and in four ambient stations
but on a different day for the chlorinated STP ED test
controls, the most logical explanation seems to be
that the control animals in the STP ED tests were a bit
more resistant. There was, however, a 20 percent
mortality in these controls the same day as the
mortality which occurred at ambient Station 2.
Young production was much lower at Stations 3 and
5, and was much higher than any upstream stations
at Stations 8A and 9. The high number of young at
these latter stations undoubtedly reflects the nutrient
enrichment from upstream and the increased food (in
the form of bacteria) levels in the absence of toxic
materials. There was very little input to the stream
below the outfalls so the reduced toxicity was probably
due to degradation and other loss factors rather than
dilution.
The young production data at Stations 2 through 6 is
affected by the toxic slug and therefore is not only the
result of the effluents present.
Table 4-8. Mean Young Production and Percent Survival of Ceriodaphnia for the Ambient Toxicity Tests in 1982
Young/ Final Daily Survival (%)
River Female Survival
Station Station Description Kilometer (x) SO (%) 1 2 3 4 5 6 7
1 Above lima 74.0 15.5 8.0 90 100 100 100 90 90 90 90
2 Above STP 60.7 14.1 2.1 0 100 100 100 100 90 10 0
3 Below STP 60.3 0 0 100 100 10 0 0 0 0
3A Midway between STP and refinery 60.2 0 0 100 100 10 0 0 0 0
3B Above refinery 59.7 0.4 0 90 90 40 0 0 0 0
4 Above chemical plant 59.4 7.5 3.6 10 100 100 100 100 100 50 10
4A Below chemical plant 58.4 11.1 4.6 30 100 100 100 100 100 40 30
5 Shawnee Bridge 57.1 5.7 4.0 0 90 90 90 90 90 60 0
6 Route 117 52.5 12.6 3.8 10 100 100 100 100 100 100 10
7 Allentown 46.3 16.8 6.1 100 100 100 100 100 100 100 100
8 Rimer 25.7 17.4 9.5 80 100 90 90 90 90 80 80
SA "Boonie" Station 12.9 25.0 3.3 100 100 100 100 100 100 100 100
9 Kalida 1.6 25.6 5.5 100 100 100 100 100 100 100 100
4-5
-------
30
Figure 4-4. CeriodBphniB young production for ambient stations, Lima, Ohio, 1982.
25
~
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E
af 20
Q;
c.
C>
c:
~
~ 15
c:
..
QI
~
10
5
2
3
3A
38
River Station Number
4.4 Evaluation of Toxicity Impacta
The results of these laboratory tests showed that the
concentrations of STP effluent that are toxic to
Ceriodaphnia are exceeded below the STP outfall in
the river, but that there is no toxicity to fathead
minnows. The concentration of refinery effluent
below that outfall is high enough to produce adverse
impact on fathead minnows, The effect level of the
refinery waste plus the STP waste in the dilution
water is less than the concentrations existing in the
stream' below the refinery and therefore toxicity to
Ceriodaphnia in the river would be expected. From
the refinery/Lake Superior water tests, the no effect
level lies between 10 and 50 percent. The concentra-
tion of refinery effluent in the river below the outfall is
29 percent. To determine if refinery waste alone
would be toxic to Ceriodaphnia below the outfall in
the river if no STP effluent were present. tests of
refinery waste without STP effluent and closer
spacing of effluent concentrations would be needed.
The toxicity contributed by the chemical plant effluent
in the river cannot be assessed without other tests.
There is enough refinery effluent in the dilution water
to cause adverse effects on the fathead minnows and
there is sufficient STP effluent in the dilution water to
cause adverse effects on the Ceriodaphnia.
.Because control and dIlutIon water was tOXIC on some tests. the performance
01 control animals cannot be used as .. bas.s for comparison 10 test
concentratIon .n all cases
4-6
4
7
S
9
SA
4A
5
6
Tests that measure the inherent toxicity of each
effluent without the complication of other effluents
being present are needed if the contribution from
each effluent is to be assessed. If a prediction of the
impact after each discharge is required, however, the
tests must be done with the extant concentrations of
the effluent in the stream below the outfall present.
The symptoms caused by the STP and refinery effluent
were quite different for Ceriodaphnia and the effluent
causing the dominant toxicity could be recognized by
the symptomology. No toxicity of STP and chemical
plant effluents to fathead minnows was found, so all
toxicity to them could be ascribed to the refinery
waste.
The dilution studies to determine the effluent concen-
trations in'the river are a very necessary part of the
assessment. Without them, little interpretation could
be done. During this study, flow was low and stable
and had been so for some time previous to the study.
Variable flows before and during the, study would
make predictions very difficult. not because the tests
are invalid, but because the actual ambient exposure
the animals receive would not be known. In those
cases where exposure varies greatly, either as a
result of variable effluent quality or variable stream
flow, laboratory tests would have to be conducted so
as to better mimic ambient concentration variations.
The absence of waste from the industrial chemical
division of the chemical plant introduces another
-------
unknown in predicting the stream impact. The
biological survey may have measured impacts from
earlier exposure to this component if residual effects
still existed. This could cause some discrepancy
between the lab tests done in this study and the
associated field data.
The toxicity test results are confounded by the toxic
slug of water from an upstream source. This study
approach was designed to measure chronic effects
and not episodic events. Further, there is no way to
know how frequently such spills occur, and therefore,
no way to know how much they affect the instream
biota. Tests could be designed to assess such cases.
Within the limits of this study, the ambient toxicity
data indicate that the conditions in the river reach
where the discharges occur are adverse to Cerio-
daphnia and that the conditions of Station SA and 9
are not. Because dilution water inputs are very minor
downstream of the discharge, one can conclude that
the loss of ambient toxicity is due to factors other than
dilution. Visual observation of the dye additions
indicate a time-of-travel of a week or more from the
STP outfall to Station 9. This at least puts some
bounds on the half-life of the combined toxicity of the
three effluents.
The test data from the ED tests for the three effluents
and the two species show the importance of differ-
ences in sensitivity of various animal species and the
need to factor this into toxicity measurements. If only
the fathead minnows had been tested, the toxic
component in the STP to Ceriodaphnia would have
been missed completely. Yet, that toxicity may impact
other types of invertebrates substantially in the
stream.
4-7
-------
5.
Toxicity of Effluents and Receiving Water, 1983
On 7-8 July 1983, the Ottawa River was revisited for
a brief survey after operational modifications were
made to the refinery. On 8 July 1983, a 24-hour
composite sample from each of the three effluents
and grab samples from seven stream stations were
taken. These samples along with a large volume of
water from Station 1, were iced and transported back
to Duluth. Testing began on 10 July 1983 in a mobile
trailer located at the laboratory. Changes in method-
ology from 1982 to 1983 were:
1. A single 24-hour composite sample was used
for the entire test but solutions were renewed
each day.
2. A fathead minnow ambient toxicity test was run
on the stream station samples in addition to the
Ceriodaphnia test.
3. Each effluent was diluted with Station 1 water
only.
4. No unchlorinated STP effluent was tested.
The methods used in these tests are more fully
described in Appendix A.
5.1 Results
Tables 5-1, 5-2, and 5-3 contain the results of the
routine water chemistry. All dissolved oxygen (DO)
measurements were above 5 mg/liter. The pH was
Table 5-2.
Water Chemistry Data for Ambient Toxicity Test
with Fathead Minnows at Various River Stations,
lima, Ohio. 1983
Initial DO
(mg/I)
Final DO
(mg/l)
Ambient
Station pH Range x SD x
Station 2" 7.9-8.1 8.6 (0.4) 8.0
Station 3 7.9-8.0 8.6 (0.4) 7.4
Station 4 7.7-7.8 8.7 (0.5) 7.9
Station 5 7.7-7.9 8.5 (0.4) 8.5
Station 6 7.8-7.9 8.5 (0.3) 8.5
Station 7 7.8-7.9 8.6 (0.2) 8.3
Station 8 7.8-8.0 8.7 (0.4) 7.5
"For Station 1 see controls on Table 5-1.
Conductivity
SD (Jlmhos/cm)
(10) 790
(0 5) 830
(0.7) 1,480
(1.0) 1.350
(0.9) 1.210
(09) 1.220
(04) 1.050
similar for all exposures and the conductivity varied
depending on the effluent and the amount of dilution.
The data for fathead minnow 7-day survival and
weight for the three effluents diluted with Station 1
water are presented in Tables 5-4 and 5-5 and Figure
5-1. There was no measurable effect of any con-
centration of sewage treatment plant (STP) effluent
on either survival or growth. The no-effect concen-
tration for the refinery waste was between 100 and
30 percent. The growth observed in all concentrations
of the chemical plant effluent were significantly
different (P = 0.01) from the controls, but there was
not a typical dose-response curve.
Table 5-1. Chemistry Data for Three Effluents in Station 1 Water for Fatheat Minnow Larval Growth Tests, lima. Ohio, 1983
Initial DO Final DO
Percent Effluent (mg/I) (mg/l) Conductivity
Effluent (v/v) pH Range x SD x SD (JJmhos/cm)
STP 100 7.7-7.9 8.6 (0.2) 64 (0.3) 850
30 7.7-7.8 8.6 (0.2) 6.8 (0.5) 750
10 7.6-7.8 8.6 (0.1) 6.8 (0.5) 710
3 7.6-7.7 8.3 (1.0) 7.1 (0.3) 700
1 7.5-7.8 8.2 (1.0) 7.2 (0.3) 690
C" 7.5-7.9 8.7 (1.5) 7.1 (0.5) 690
Refinery 100 7.2-7.5 8.4 (0.8) 7.3 (02) 2.700
30 7.6-7.8 8.6 (0.5) 7.0 (03) 1, 280
10 7.7-7.8 8.6 (0.5) 7.0 (0.3) 900
3 7.7-7.9 8.7 (0.4) 6.7 (0.7) 750
1 7.9 8.7 (0.4) 6.9 (0.5) 690
C 8.0 8.5 (0.4) 6.8 (0.5) 690
Chemical plant 100 7.8 8.5 (0.5) 7.6 (0.7) 2.050
30 7.9 8.5 (0.7) 7.2 (0.7) 1.100
10 7.9-8.0 8.5 (0.4) 7.2 (0.4) 820
3 7.9-8.0 8.5 (0.4) 7.1 (0.3) 72.0
1 7.9-8.0 8.5 (0.4) 6.9 (0.4) 710
"Water for controls and dilution was taken from Station 1 upstream of all discharges.
5-1
-------
Table 5-3.
Final Dissolved Oxygen Concentrations for
C.riodaphnia Tests on Effluents and Stream
Station Water, Lima, Ohio, 1983
Sample
STP
% Effluent DO (mg/I)
(v/v) x SD
100 8.0 (0.7)
30 7.7 (0.5)
10 7.7 (0.5)
3 7.8 (0.5)
1 7.8 (0.5)
C 7.7 (0.5)
100 7.2 (0.4)
30 7.4 (0.2)
10 7.6 (0.3)
3 7.5 (0.2)
1 7.5 (0.2)
C 7.4 (0.2)
100 7.3 (0.3)
30 7.5 (0.3)
10 7.4 (0.1)
3 7.4 (0.1)
1 7.5 (0.1)
C 7.4 (0.2)
7.4 (0.5)
7.4 (0.5)
7.4 (0.4)
7.4 (0.3)
7.4 (0.4)
7.4 (0.3)
7.3 (0.3)
Refinery
Chemical
plant
Station 2
Station 3
Station 4
Station 5
Station 6
Station 7
Station 8
The data for the ambient toxicity to fathead minnows
show that the weights at Stations 2 and 8 were all
significantly lower (P = 0.01) than the fish in Station 1
water but not for percent survival (Tables 5-6 and 5-7
and Figure 5-2).
The data for the Ceriodaphnia young production and
survival for the three effluents diluted in water from
Table 5-4.
Seven-Day Percent Survival of Larval Fathead
Minnows Exposed to Various Concentrations of
Three Effluents in Station 1 Water, Lima, Ohio,
1983
% Effluent (v/v)
Effluent by Replicate 100 30 10 3 Control
STP
A 70 100 100 100 90 90
B 80 90 100 90 90 90
C 100 90 90 90 100 90
D 90 100 80 70 90 90
Mean 85 95 92.5 87.5 92.5 90.
Refinery
A 20 100 100 100 100 100
B 10 90 100 90 90 80
C 0 100 100 90 90 100
D 20 90 90 100 90 80
Mean 16.6b 95 97.5 95 92.5 90.
Chemical plant
A 80 100 80 80
B 100 ~ 90 W
C 70 60 70 90
D 100 W 90 ~
Mean 87.5 77.5 82.5 80
"Data for two controls pooled.
~ean of treatments significantly different (P = 0.01) from control.
70
70
90
80
77.5
90
5-2
Figure 5-1. Fathead minnow growth tests for STP, refinery, and
chemical effluents, Lima, Ohio. 1983.
100
01
>
.~ 60
::J
IJ)
E
CD
:: 40
CD
a..
Ci
.s 0.6
.E
C>
'Qj
~
> 0.4
Q
c:
01
CD
~
-----------------------
\
\
,
,
','
."
, ,
\
\
\
\
,
\
\
\
\
,
\
\
\
\
\
\
\
\
\
\
,
\
,
\
\
'.
80
Percent Survival
20
-=STP
-----_. = Refinery
. ....., = Chemical Plant
o
0.8
1
Growth (dry weight)
STP
Refinery
.......... = Chemical
10
100
0.2
--'
.--- ----------------- "
uu>\
\
\
\
\
\
\
\
\
o
100
1 10
Percent Effluent (vol/vol)
Station 1 are shown in Table 5-8 and Figure 5-3. The
no-effect level was between 10 and 3 percent for both
the refinery and the STP while no concentration ofthe
chemical plant produced an effect.
Table 5-9 and Figure 5-4 contain data for Ceriodaph-
nia survival and young production for the ambient
toxicity test. Stations 3 through 7 were significantly
different (P = 0.01) from Station 2 but Station 8 was
not different.
The data for the estimated effect concentrations for
the three effluents and two species are given in Table
5-10. Table 5-11 presents the estimated concentra-
tions of STP and refinery effluent in the Ottawa River
below each outfall based on conductivity. Conductiv-
ity at Station 5 was less than the conductivity at
Station 4 and. therefore, the dilution of the chemical
plant effluent cannot be calculated. In 1982, the
chemical plant made up <10 percent of the river and
conditions were similar in 1983.
-------
Table 5-5. Mean Weight (mg) of Larval Fathead Minnows Exposed to Three Effluents at Various Concentrations, Lima, Ohio,
1983
% Effluent (v/v)
Effluent by
Replicate 100 30 10 3 Control
STP
A 0.450 0.400 0.445 0.410 0.522 0.511
B 0450 0.567 0.475 0.539 0.498 0.478
C 0.470 0.483 0.470 0.478 0.490 0.500
D 0.483 0.520 0.494 0.443 0.456 0.544
Mean 0.46 0.49 0.47 0.47 0.49 0.47"
SD (0.02) (0.07) (0.02) (0.06) (0.03) (0.03)
Refinery
A 0.075 0.410 0.560 0.405 0.470 0.435
B 0.050 0.411 0.440 0.461 0.472 0.386
C 0.345 0.545 0.511 0.378 0.435
D 0.175 0.411 0.406 0.425 0.472 0.444
Mean 0.1" 0.39 0.49 045 0.45 0.47"
SD (007) (0.03) (008) (0.05) (0.05) (0.03)
Chemical plant
A 0.281 0.310 0.338 0.275 0.286
B 0310 0.325 0.294 0.343 0.364
C 0.279 0.275 0.314 0.333 0.317
D 0.265 0.271 0.275 0.363 0.412
Mean 0.28" 0.30" 0.31 b 0.33" 0.34" 0.47"
SD (002) (003) (0.03) (0.04) (0.06) (0.03)
"Data for two controls pooled.
"Mean of treatments significantly different (P = 0.01 ) from control.
Table 5-6.
Seven-Day Percent Survival of Larval Fathead
Minnows Exposed to Waterfrom Various Stream
Stations for Ambient Toxicity, Lima, Ohio, 1983
Stream Station
Replicate 1" 2 3 4 5 6 7 8
A 100 80 90 80 90 100 90
B 100 100 90 90 90 80 90
C 80 90 60 80 90 90 80
D 100 70 70 100 80 90 90
Mean 90 95 85 775 87.5 87.5 90 87.5
"Data for Station 1 are the same as for controls on Table 5-4.
5.2 Discussion
Concentrations of STP and refinery waste in the
stream were less than the minimum predicted effect
levels for fathead minnows (Tables 5-10 and 5-11 ).
The ambient toxicity data as depicted by Figure 5-4
does not suggest an increase in toxicity below either
the STP or refinery outfall (Stations 3 and 4) as
compared to Station 2 which is above both outfalls.
However, all three stations and Stations 5 through 8
were less than Station 1 .
For Ceriodaphnia, both the STP and the refinery
concentrations were greater in the river than the
estimated effect concentrations, but the chemical
plant concentrations was not. The ambient toxicity
data in Table 5-8 show significant toxicity below the
Table 5.7.
Meen Weight (mg) of Larval Fathead Minnows Exposed to Water from Various Stream Stations for Ambient Toxicity,
Lima, Ohio, 1983
Replicate 1" 2 3
A 035 0.27
B 036 0.25
C 0.37 0.34
D 0.30 0.34
Mean 0.47 0.34" 0.30"
SD (003) (0.03) (005)
"Data for Station 1 are the same as for controls on Table 5-5.
"Significantly different (P = 0.01) from controls in effluent test (Station 1 water).
Stream Station
4
038
0.32
0.28
0.36
0.34"
(004)
6
0.28
0.33
0.26
0.32
0.30"
(0.03)
7
0.30
037
0.31
0.37
0.34"
(0.04)
8
0.34
0.33
0.37
0.26
0.33"
(0.05)
5
0.31
0.39
030
0.35
0.34"
(0.04)
5-3
-------
Figure 6-2.
'"
>
.~ 60
:J
en
C
Q)
~ 40
0..
100
80
20
Fathead minnow growth tests for ambient
stations, lima, Ohio, 1983.
'~~
~0.6
E
CI
Qj
3: 0.4
>-
C
c:
'"
Q)
~0.2
~ 30
'"
E
Q)
~
Q;
~ 20
c:
:J
o
>-
c:
~ 10
~
0.8
Figure 6-3.
40
2
4
6
2
4 6
River Station Number
8
8
C",iodephnie young production in three efflu-
ents, lima, Ohio, 1983.
................,
.".,....................................... .
--------------------------
"\
,
\
\
\
\
,
\
\
\
\
\
= STP Effluent
-----_. = Refinery Effluent
............. = Chemical Effluent
o
1 10
Percent Effluent (vol/vol)
5-4
100
Mean Young Per Female C",iod"phni" and Mean
7-Day Percent Survival of Original Test Animals
Exposed to Various Effluent Dilutions in Station
1 Water, lima, Ohio, 1983
% Effluent 7-Day Survival
(v/v) (%)
100 0
30 30
10 90
3 100
1 100
Contra'" 93
1 00 70
30 1 00
10 100
3 80
1 80
Control 93
100 100
30 1 00
10 100
3 100
1 100
Control 93
"Control data for all three combined.
.Significantly different (P = 0.01 ) from combined controls.
Table 6-8.
Effl uent
STP
Refinery
Chemical plant
10
Table 6-9.
Young/Female
x SD
0.30. (0.95)
10.6. (4.5)
17.0. (10.0)
24.5 (3.2)
25.2 (2.2)
24.6 (7.1)
0.0.
0.0.
14.7. (7.9)
18.5 (11.0)
20.2 (116)
24.6 (7.1)
27.7 (7.4)
29.1 (6.8)
28.8 (3.2)
29.2 (2.6)
24.6 (3.1)
24.6 (7.1)
Mean Young Per Female C",iod"phni" and 7-Day
Percent Survival of Original Test Animals Exposed
to Water from Various Stream Stations for
Ambient Toxicity, lima, Ohio, 1983
10
Station No.
1
2
3
4
5
6
7
8
7-Day Survival
(%)
93"
100
o
90
20
100
10
100
Young/Female
x SD
24.6" 7.1
29.2 7.1
2.7. 2.5
11.9. 4.6
8.4. 5.3
4.2. 2.6
6.8. 5.6
27.9 3.3
"Average of three sets of effluent controls.
.Significantly different (P = 0.01 ) from Station 2.
Table 6-10.
Geometric Mean of the Effect and No Effect
Concentration for the Three Effluents and Two
Test Species, lima, Ohio. 1983
Species Effl uent Geo. Mean
Fathead STP >100%
minnow Refinery 54.8%
Chem. plant ?
Ceriodaphnia STP 5.5%
Refinery 5.5%
Chem. plant >100%
-------
Table 5-11.
3
4
Predicted Concentrations of STP and Refinery
Effluent at Near-Field Stations Based on Con-
ductivity Measurements, Lima, Ohio, 1983
STP Refinery
66% 0%
44% 34%
Station
Figure 5-4. Ceriodaphnia young production for ambient
stations, Lima, Ohio, 1983.
40
Q)
'iii 30
E
Q)
u.
Cii
Q.
g' 20
:J
o
>-
c:
'"
Q)
:2 10
/.
,
2
,
4
,
6
,
8
,
10
River Station Number
STP and below the refinery as well as downstream to
Station 8 as the effluent data would suggest. Thus
from both sets of tests the Ceriodaphnia data predict
impact in the river below the STP and downstream
until Station 8 where the toxicity disappears.
The fathead minnow data for the chemical plant
effluent cannot be easily interpreted. Since there was
no clear dose-response curve, one cannot attribute
the toxicity observed, which was not severe, to the
chemical plant effluent.
The fathead minnow ambient toxicity data could be
explained by a slightly toxic substance in the water
that entered above Station 2. Indeed, in the 1982
study, a toxic slug was observed to have entered
above Station 2. Since the 1983 study was performed
on one grab sample, a clear-cut explanation cannot
be readily provided.
5-5
-------
6.
Dilution Analysis of the Sewage Treatment Plant, Refinery, and Chemical Plant,
1982
A dye study was performed at each of three sites
(Table 6-1) to identify the individual dilution charac-
teristics of each effluent. By modeling downstream
dilution contours for each discharger, the exposure
concentration pertinent to instream effects could
then be quantified.
6.1 Sewage Treatment Plant (STP)
The STP is located on the right (northwest) bank of the
Ottawa River at approximately RK 60.5 and has a
nominal flow of 0.53 m3/sec (12 mgd). During the six
days onsite, 20-25 September, daily average flows
varied from 0.335 to 0.417 m3/sec (Table 6-2). On 20
and 21 September, during the STP dye study, daily
average flows were 0.358 and 0.36 m3/sec, respec-
tively. Plant-operational data during 22-25 Septem-
ber, provided by the STP, indicate that flows usually
decrease by several mgd during the early morning
hours, reaching a minimum between 0600 and 0800
hours, and then increase until 1200 hours. The STP
was not as consistent during the afternoon with flows
either maintaining their level recorded at 1200 hours,
or decreasing until 1800 hours. The STP has storage
capacity sufficient to allow the discharge flow to be
regulated independently of the inflow under a variety
of conditions.
Injection of Rhodamine WT dye started at approxi-
mately 1400 hours on 20 September and continued
until 1545 hours on 21 September. The two Fluid
Metering Inc. precision metering pumps were con-
nected to a 200-gm/liter container of dye and a 400-
gm/liter solution of Na2S203, respectively. The line
from the dye was inserted through the side wall of the
larger line from the Na2S203 and both lines were
lowered down a manhole approximately 36 m from
the STP discharge into the Ottawa River. The
resulting dye injection rate was calculated to be
approximately 5.0 ml/min. The Na2S203 injection
rate of 240 ml/min is equivalent to a 4.45 ppm
concentration in a discharge flow of 0.36 m3/sec,
which would protect the dye from a chlorine residual
of 0.7 ppm. During the two-day study, the chlorine
residual was nominally held below 0.2 ppm.
The instream water samples were collected on 21
September from 1045 to 1440 hours at the 13
Table 6-1. Transect Locations for the Dye Dilution Analysis
atThree Sites on the Ottawa River. 1982 Survey
Distance
Distance from
Distance from Chemical
from STP Refinery Plant
Transect (m) Transect (m) Transect (m)
TOa -107
TOb -40
n 0
T2 15
T3 30
T4 76
T5 137
T6 213
T7 305
T8 457
T9 762
TO -30
853 n 0
T2 15
T3 30
no 930 T4 76
T5 137
T6 213
T7 305
TOa -61
TOb -30
1.265 410 T1 0
T2 9
T3 30
T8 457 46
T4 76
T5 137
T6 213
n1 1,524 671 259
T9 762 T7 351
T10 1,067 T8 655
n1 1,524 T9 1,113
T10 1,311
n1 1.433
transects described in Table 6-1. The observed
background fluorescence was 0.05 ppb at the up-
stream velocity transect (152 m above the discharge)
and 0.3 ppb in the STP discharge prior to dye
injection. The background fluorescence applied to the
transect data was e)(trapolated between these two
values in proportion to the observed dye concentra-
tion in each sample. The dye injection rate and
average plant flows for 20 and 21 September result in
calculated average discharge dye concentrations of
46.5 and 46.1 ppb, respectively.
6-1
-------
~ T~ l~ ~15:J/ TOa j~
3.ct°'0~
..~~ 3.0
2.0 18/
. TOb 5.0 TOb
_n- Riffle Area ----Riffle Area
Om T1 Om
T2 T2
T3 T3
Flow Flow
The average dye concentration measured at the point
of discharge was 48.8 ppb on 20 September from
1430 to 2400 hours and 53.3 ppb on 21 September
from 0000 to 1530 hours. The predicted concentra-
tions are in reasonable agreement with measured
concentrations considering that they were based on
daily average plant flows. During the early morning
hours the reduced plant flow (0.20 m3/s.ec at 0633 on
21 September) results in greater discharge dye
concentrations. On 21 September it is likely that the
actual flow for the period 0000-1530 hours was
sufficiently below the daily average flow to account
for the observed 15 percent increase in dye con-
centration. The average dye concentration recorded
at the discharge between 1130 and 1230 hours on 21
September, the time when Transects T1-T4 were
Figure 6-1. Surface dilution contours in the Ottawa River
downstream from the STP, 21 September 1982.
200m }------------ TO
300m
T7
6-2
sampled. was 49.6 ppb. This value was used to form
all dilution ratios since it accurately represents
conditions while the near-field transects were being
sampled and is a compromise between higher early
morning values and lower daily average values for
downstream transects which have a longer time
history. The resulting dilution contours are shown for
the surface (Figure 6-1) and for the bottom (Figure
6-2).
For depths less than 0.5 m, the same value (0.2 m
from bottom) is used in each figure. Multiple depths
were recorded primarily at Transects TOa and TOb
upstream of the discharge and at T1 at the discharge.
These figures indicate that the freshwater inflow at
the top of the pool is overridden by a surface layer of
Figure 6-2. Bottom dilution contours in the Ottawa River
downstream from the STP, 21 September 1982.
200 m
T6
- ------------
300 m
T7
-------
STP effluent, which extends upstream of the dis-
charge. On the surface, a dilution contour of 2
extends 45 m upstream toward the head of the pool.
whereas on the bottom a dilution factor of 2 extends
downstream to the discharge. The effluent remained
at a dilution less than or equal to 1.2 (83 percent of
river flow) along the right bank for 120 m. After the
first riffle area, approximately 90 m downstream of
the discharge, the effluent mixed across, approaching
the fully-mixed state at a dilution ratio of 1.3 (77
percent of the river flow about 210-245 m down-
stream). On 21 September, a flow of 0.071 m3/sec
was measured upstream ofthe plant. Thisflowvalue,
coupled with the daily average plant flow of 0.361
m3/sec, implies that the STP makes up 83.6 percent
of the downstream flow during these seasonal flow
conditions of the Ottawa River (Table 6-3). It is
believed that the STP flow was less than the daily
average value during and preceding the survey,
indicating that the smaller value of 77 percent calc-
ulated from the dye study reflects these conditions.
6.2 Refinery
The refinery discharge is located on the left (south-
east) bank of the Ottawa River 850 m below the
discharge from the STP (approximately RK 59.7). The
refinery has a nominal flow of 0.24 m3/sec (5.5 mgd).
The discharge flow is recorded on a 7 -day circular
chart from which the values every three hours were
tabulated for the period 20-25 September. The daily
average flow during this 6-day period ranged from
0.201 m3/sec on Tuesday to 0.099 m3/sec on
Saturday (Table 6-2). During any given day, the flow
was fairly steady except on Thursday, 23 September,
when the flow decreased after 1200 hours.
The injection of Rhodamine WT dye started at
approximately 1210 hours on 22 September and
continued to 1410 hours on 23 September. The
metering pump was connected to a 70.7 gm/liter
container of dye, injected just above the weir in the
Table 6-2.
River Flows Upstream of the STP and Reported
Discharge Flows at Each Site. 1982 Survey
Flow (m3/sec)
STP Refinery Chemical Plant
0.358 0 187
0.361 0.199
(NA)a
0.335
0.372
(0.218)a
0.417
0.358
(0.277)a
aAverage flow for period preceding and during initial instream
sampling when different from daily average.
Note: N.A. = not available.
Date
20 Sept.
21 Sept.
Upstream
0.071
0.068
0.055
22 Sept.
23 Sept.
24 Sept.
25 Sept.
0.201
0.173
(0.189)a
0.106
0.099
0.059
0.064
0.062
0.069
0.123
0.137
discharge canal at a location approximately 210m
from the river. Dye was injected at a rate of 4.96
ml/min. Midway between the weir and the river was
a small basin where the continuous discharge
fluorometer was installed just ahead of the outlet
culvert.
Instream water samples were collected along the
transects described in Table 6-1 from 0930 to 1230
hours on 23 September. Average background fluo-
rescence at Transect TO. upstream of the discharge.
was 0.36 ppb. The background fluorescence in the
discharge canal prior to initiation of dye injection was
0.15 ppb. A flow-weighted background fluorescence
of 0.29 ppb was used downstream of the discharge
for most samples. The average discharge dye con-
centration calculated from the dye injection rate and
the three hourly discharge flows was 30.35 ppb
between 1500 hours on 22 September and 1200
hours on 23 September. During the same time
interval, the average dye concentration recorded at
the discharge was 30.10 ppb. which is in excellent
agreement with the calculations.
Due to the uniform discharge flow, the discharge dye
concentration showed little variability during and
preceding the instream survey. An average discharge
concentration of 30.4 ppb (0000-1030 hours on 23
September) was used to form the dilution ratios.
Dilution contours downstream from the discharge are
presented in Figure 6-3. These contours indicate a
prominent discharge jet extending at right angles to
the bank. The discharge influence extends to the
opposite bank at the point of discharge with uniform
surface and bottom values. The high initial mixing
may be aided by a fallen tree, which lies across the
river 23 m below the discharge. An eddy was
observed, with water movement along the obstruc-
tion toward the discharge bank then upstream to be
re-entrained in the discharge. The remaining mixing
occurred more slowly with the discharge approaching
fully-mixed at a dilution ratio of 2.65 approximately
365 m below the point of discharge. This ratio
corresponds to the effluent comprising 38 percent of
total flow. The effluent was diluted by the chemical
plant discharge at 41 0 m and the river again became
fully-mixed at 760 m.
To compare the observed dilution ratio with the flows,
adjustments need to be made to the daily average
values in order to represent survey conditions. The
discharge flow decreased noticeably after 1200
hours, so an average flow of 0.189 m3/sec from 0000
to 1200 hours was used. The discharge flow of the
STP from 0515 to 1030 hours was too low to be
recorded properly on the 15-minute computer print-
out. The daily minimum flow of 0.16 m3/sec was
reported at 1019 hours and all flows during this
period (0515-1030 hours) were most likely less tha n
6-3
-------
Figure 6-3. Dilution contours in the Ottawa River downstream
from the refinery, 23 September 1982.
10 m
----Riffle Area
Flow
~TO
1\11
,0
13
T7
50 -'
Om .~~ ~T1
( 2.0- ~T2 2.6
"
.4 rT3
: 26 400m
, 27 2.5 0
I
I T4
2.8
100 m
T8
T5
200 m
T6
\
600m
300 m
T7
0.22 m3/sec, the value used here. These flows,
coupled with a measured stream flow of 0.123
m3/sec above the STP, combine to give a flow of
0.531 m3/sec below the discharge during the in-
stream survey. The flow (0.189 m3/sec) is 35.6
percent of this total flow, illustrating that the dye
results are in reasonable agreement with the ob-
served flows (Table 6-3). At Transect T11, 1,524 m
below tl1e discharge, a gradient exists with dilution
increasing from mid-channel to the banks. This lack
of equilibrium is probably an artifact of the reduction
in flow occurring in the early morning hours at the
STP. The higher dilution ratios observed near the
bank are from water parcels which were passing the
discharge before the early morning flow reduction
occurred at the STP
6.3
Chemical Plant
The chemical plant discharge is located on the left
(southeast) bank of the Ottawa River, approximately
RK 59.2. The discharge is 410 m below the refinery
discharge and 1,265 m below the STP. The chemical
plant discharge has a nominal flow of 0.088 m3/sec
(2 mgd). From 20 to 25 September, the reported daily
average flow ranged from 0.055 to 0.069 m3/sec
(Table 6-2). The flow at the chemical plant discharge
is nominally steady over a day.
The injection of Rhodamine WT dye started at 1045
hours on 24 September and continued to 1440 hours
Table 6-3.
Ottawa River Flow and Percent Flow Contribution from the Discharges on the Days of the Three Dye Surveys. 1982
Survey
Percent Flow Contribution"
Flow
(m3/sec) Upstream STP
21 Sept (STP Survey)
Below STP 0432 16.4 83.6
Below refinery 0.632 11.2 57.2
Below chemical plant 0686 10.3 52.7
23 Sept (Refinery Survey)
Below STP 0.495 24.9 75.1
(0342). (362) (63.8)
Below refinery 0668 18.5 55.6
(0531) (233) (41.1)
Below chemical plant 0732 16.9 50.8
(0594) (20.8) (36.7)
25 Sept. (Chemical Plant Survey)
Below STP 0.495 276 72.4
(0.414) (330) (67.0)
Below refinery 0.594 23.0 603
(0.513) (267) (54.0)
Below chemical plant 0.662 20.7 54.0
(0582) (235) (477)
Refinery
Chemical
Plant
31.6
29.0
8.0
25.9
(35.6)
23.6
(31.B)
8.7
(10.7)
16.7
(19.3)
15.0
(17.0)
10.3
(11.8)
"Values also represent percent contribution of effluent at fully-mixed zone for each discharger.
Example Below STP on 21 September
83 6 percent flow contribution x 49.6 ppb STP discharge concentration
= 41.5 ppb fully mixed concentration 738 m downstream.
"Average flow for period preceding and dUring Initial Instream sampling when different from daily average.
6-4
-------
on 25 September. At approxi mately 1245 hours on 24
September the metering pump was reset to give a
lower injection rate. The metering pump was con-
nected to a 70.7 gm/liter container of dye. injected
into a culvert across the road from the discharge
house and approximately 60 m from the river. The
continuous discharge fluorometer was installed at
the discharge house. Monitoring of dye weight
showed a dye injection rate of 2.86 ml/min.lnstream
water samples were collected on 25 September
between 0915 and 1240 hours along the transects
described in Table 3-1. Average background fluo-
rescence at Transects TOa and TOb was 0.19 ppb.
whereas the background fluorescence in the chem-
ical plant discharge prior to the dye injection was 0.05
ppb. A flow-weighted background fluorescence of
0.17 ppb was used downstream from the discharge.
The daily average discharge flow on 24 and 25
September of 0.062 and 0.069 m3/sec results in a
predicted dye concentration at the point of discharge
of 54.6 and 49.0 ppb. respectively. The recorded
discharge dye concentration was 53.5 ppb on 24
September (1300-2330 hours) and 48.9 ppb on 25
September (0000-1430 hours). An average discharge
dye concentration of 49.9 ppb (0000-1030 hours).
representative of the preceding time history. was
used in forming dilution ratios. The dilution ratios
downstream of the chemical plant discharge are
presented in Figure 6-4.
The plume remained along the left bank for approx-
imately 120 m before beginning to mix the rest of the
way across. From 460 to 760 m. the river is
approximately fully-mixed at a dilution ratio of 7.1.
although the far bank (right) continues to display
slightly higher dilution (i.e.. lower dye concentra-
tions). A dilution ratio of 7.1 corresponds to the
chemical plant effluent that is 14 percent of the river
flow. The total river flow below the chemical plant
discharge corresponding to its time history is 0.582
m3/sec. This number is composed of 0.137 m3/sec
measured. above the STP. 0.277 m3/sec at the STP
during the morning hours. and the daily average
flows at the refinery and chemical plant of 0.099 and
0.069 m3/sec. respectively. These reported flow
values correspond to the chemical plant effluent
making up 11.8 percent of the river flow on 25
September (Table 6-3).
6.4 Evaluation of Dilution Characteris-
tics
The Ottawa River flow and the fully-mixed (percent)
flow contribution below each discharge from each
upstream source is summarized in Table 6-3 for the
dates of the three dye surveys. Table 6-3 a Iso reflects
percent concentration of effluent at the fully-mixed
zone for each of the dischargers. Individual contribu-
tions vary among days. primarily as a result of the
Figure 6-4. Dilution contours in the Ottawa River downstream
from the chemical plant. 25 September 1982.
----- Riffle Area
l~
TOa
Flow
Om
T5
200m
T6
upstream flow increasing from 0.071 to 0.137
m3/sec. whereas the refinery discharge decreased
from approximately 0.20 to 0.10 m3/sec during the
study period. As discussed in Sections 5.1-5.3. the
contribution at any given time is different from the
daily average value due to the hourly flow variations
at the STP The effluent contributions to the receiving
water based upon the average flows observed during
the study period. 20-25 September. are illustrated in
Figure 6-5.
Under the low upstream flow condition of the study.
the STP strongly influenced the pool into which it
discharged. Above the discharge more dilution oc-
curred on the bottom because ofthe upstream inflow.
6-5
-------
Figure 6-5. Effluent contribution to receiving water.
0.8
0.6
~
!l 0.4
u..
0.2
Stations
whereas on the surface, water with a dilution of 2
extended 45 m towards the head of the pool. The STP
effluent was fully-mixed 245 m downstream of the
discharge. The average STP flow comRosed 83
percent of the river on the study day and decreased to
72 percent four days later as a result of increased
upstream inflow. The refinery discharge had a
prominent jet at right angles to the bank with the
majority of the mixing occurring in the first 60 m. The
river gradually became fully-mixed 365 m below the
discharge, just above the chemical plant discharge.
During the days of the three dye studies, the refinery
discharge ranged from 16.7 to 31.6 percent of the
river flow, whereas the STP ranged from 55.6 to 60.3
percent of the river flow below the refinery. For the
first 120 m downstream from the chemical plant
discharge, this effluent was confined to one-third of
the river's width. The majority of the mixing of the
chemical plant effluent with the STP/refinery water
occurred by 245 m, and the river gradually ap-
proached the final fully-mixed state 760 m down-
stream from the discharge. Here the chemical plant
effluent comprised 8-10 percent of the river flow,
whereas the refinery contributed 15-29 percent and
the STP 51-54 percent during the days of the three
dye studies.
Additional flow measurements in the study area are
available for four days in September 1979 (Engi-
neering-Science 1981). These data indicate that the
average upstream river flow above the STP flow was
0.487 m3/sec, whereas the average STP flow was
0.459 m3/sec. Under these conditions of increased
upstream flow, the fully-mixed STP effluent was 49
percent of the river flow. During the same period, the
average flow measured at Allentown, Ohio was 1.44
m3/sec. The United States Geological Survey reports
a 44-year average discharge at Allentown of 3.57
m3/sec (USGS 1976). The USGS data for water-year
1975 indicates monthly average December March
flows ranging from 5.04 to 15.46 m3/sec, whereas
flows in summer and fall ranged from 0.75 to 2.05
6-6
m3/sec. These data indicate that the flows reported
by Engineering-Science are probably representative
of typical fall conditions. whereas the low upstream
flows of 0.071 to 0.137 m3/sec observed by EPA
more likely represent a low-flow event.
A low-flow 70/ 10 event cannot be addressed directly
since a 70/10 flow is not available for the Ottawa
River above the STP. Under any worst case condition,
the STP flow will dominate the river flow such that at
a ny poi nt below the STP discha rge the upstrea m river
flow could be approximated by the STP flow (i.e.,
assume zero upstream flow). During the 6-day study
period, average flows at the STP, the refinery, and the
chemical plantwereO.367, 0.161, andO.063 m3/sec,
respectively. Under these conditions, the STP effluent
would make up 100 percent of the river above the
refinery (93 percent with a 0.028 m3/sec (1 cfs)
upstrea m flow). Downstrea m of the refi nery, the river
would be 70 percent STP and 30 percent refinery.
Downstream of the chemical plant, the river would be
62 percent STP, 27 percent refinery, and 11 percent
chemical plant. Only the STP contribution would
change by more than 1 percent if a 0.028 m3/sec (1
cfs) upstream flow had been used.
-------
7.
Periphytic Community, 1982 Survey
An effect on the periphytic community may be seen in
either a reduction of an important habitat or food
source for invertebrates and fish or the enhancement
or dominance of nuisance species of algae that
neither support lower trophic levels nor are aesthet-
ically pleasing. The following discussion is intended
to present an overview of the response of the
periphytic community to the discharges. Support
periphyton data on the composition and abundance
are presented in Appendix Tables 0-' and 0-2.
Methods used in the periphyton studies are in
Appendix Section C. , .
7.1 Community Structure
Periphyton communities at each station were numer-
ically dominated either by diatoms or green algae
(Table 7-' ). Station' at Thayer Road was character-
ized by low periphyton density, high diversity, and
high equitability relative to the other sampling
locations (Figure 7-'). Total density increased nearly
three-fold at Station 2 upstream from the Lima
Sewage Treatment Plant (STP), diversity was the
highest observed at any station (partly because ofthe
greater number of genera observed), and equitability
declined somewhat although it was still moderately
high. Composition of dominant taxa was similar to
that observed at Station' .
At Station 3 between the Lima STP and the refinery,
periphyton abundance exhibited a pronounced five-
fold increase over that observed at Station 2. All of
this increase was caused by Stigeoclonium (Figure
7-2), and as a result diversity and equitability were
extremely low at Station 3. Except for blue-green
algae, which were absent at this station (Table 7-'),
other taxa that were important at the upstream
stations persisted at reduced densities. Total density
at Station 4 between the refinery and the chemical
plant was very similar to that observed at Station 2
(56,000 cells/mm2). Diversity and equitability were
moderate, and the diatom Nitzschia was clearly
numerically dominant at Station 4. Several other taxa
that were important at Station 2 were at least
moderately abundant at Station 4.
Immediately downstream of the chemical plant at
Station 5, total periphyton density was unchanged,
but the green alga Stigeoclonium was once again
abundant. Diversity and equitability were again very
low, although values for these indices were not as
low as those observed at Station 3. Periphyton
Table 7-1. Summary of Periphyton Composition, Diversity, and Standing Crop on Natural Substrates in the Ottawa River,
September 1982
Sampling Stations
Parameter 2 3 4 5 6 7 8 9
Density (cells/mm2)
Diatoms 12,670 33,022 7,382 42,295 2,494 25.137 30,824 32,321 7,382
Green algae 3,791 13,367 245,488 9,079 52,570 62,544 10,475 6,285 4,290
Blue-green algae 2,095 8,679 0 4,289 0 2,195 4,988 1,796 898
Total Periphyton 18,556 55,168 252,970 55,763 55,064 89,876 46,287 40,402 12,570
Percentage of Total Density
Diatoms 68.28 59.86 2.92 75.85 4.53 27.97 66.59 80.00 58.73
Green algae 20.43 24.33 97.04 16.28 95.47 69.59 22.63 15.56 34.13
Blue-green algae 11.29 15.73 0.00 7.69 0.00 2.44 10.78 4.45 7.14
Taxa (Genus) Diversity (d) 2.91 3.29 0.28 2.63 0.42 1.76 2.25 2.71 2.92
Taxa (Genus) Eqllitability (e) 0.95 0.67 0.09 0.45 0.19 0.25 0.46 0.60 0.81
Total Genera Identified 11 21 13 19 8 17 14 15 13
Chlorophyll a (mg/m2) 31.9 273.6 296.5 193.8 111.7 151.0 166.6 135.9 102.4
Biomass (g/m2) 22.2 61.8 35.9 29.8 19.5 39.6 19.6 232 18.7
Autotrophic Index (Weber 1973) 971 230 135 176 216 269 119 225 208
7-1
-------
Figure 7-1. Spatial distribution of periphyton community indices and associated parameters, 1982 survey.
Periphyton
Ottawa River
3.5
30
2.5
)(
~ 20
c
15
1.0
0.5
en
II>
c:; 15
II>
c.
~ 12
o
o
Z 9
o
Flow
No. of Individuals
No. of Taxa
o Receiving Waters
~STP
~ Refinery
. Chemical Plant
, -
"'------ ---------
---- ---
24
234 5
(253.000)
~
7
6
21
18
/
/
/
/
/
6
3
Refinery
Stations
composition was considered similar at Stations 3 and
5 because Stigeoclonium dominated, diatoms com-
posed less than 5 percent of total density, and blue-
green algae were absent at these sampling locations
(Table 7 -1 ). At Station 6 further downstrea m from the
chemical plant. total density increased to approxi-
mately 90,000 cells/mm2. Diversity and equitability
also were higher than observed at Station 5, but
values for these indices of community structure were
still moderately low. Stigeoclonium numerically
dominated the periphyton at Station 6, but the diatoms
Achnanthes, Navicula, and Nitzschia were also
important components of the community.
At Station 7 near Allentown, total density declined by
approximately 50 percent. whereas diversity and
equitability increased to moderate levels. Stigeoclon-
ium declined in abundance but remained an important
component of periphyton. The community was domi-
7-2
- Diversity
8
8
9
1 20,000
105,000
90,000 c
(II
~
75,000 III
;:0'
-<
60,000 n
!!.
en
"-
45.000 3
1
30,000
15,000
0
9
nated by Nitzschia. although Navicula and filamen-
tous blue-green algae were also abundant (Table 0-
1). Twenty kilometers farther downstream at Station
8, total density remained similar to that observed at
Station 7, but diversity and equitablity increased to
moderately high values. Navicula was the most
abundant genus; Nitzschia and Stigeoclonium were
also important periphyton constituents (Table 0-1).
At Station 9, the farthest downstream station,
periphyton abundance was similar «20,000 cells/
mm2) to that recorded at the upstream control (Station
1 ). Diversity at these stations was essentially identical
(2.92 vs. 2.91), and equitability at Station 9 was high
(Table 7-1). There were, however, differences in
composition between Stations 1 and 9, although
Navicula and Nitzschia were important at both
stations (Table 0-1 ).
-------
7.2 Chlorophyll a and Biomass
Chlorophyll a standing crop in the Ottawa River
ranged from approximately 32 to 296 mg/m2; biomass
standing crop varied from 19 to 62 g/m2 (Table?-1).
Chlorophyll a was significantly lower at St.atlon 1
than at all other stations. The high Autotrophic Index
(AI) value at Station 1 combined with the '?w chloro-
phyll a values indicated periphyton either was
primarily composed of heterotrophic .(nonalgal).t~xa
or contained a relatively large proportion of nonliving
organic matter (APHA 1981). However, low algal
standing crop (as indicated by chlorophyll a.l was mo~e
responsible for this high AI value than any Increase In
heterotrophic or nonliving biomass. Based on data
from the other sampling locations, AI values less than
approximately 250 appeared to be typical for the
Ottawa River in this September survey.
Maximum biomass standing crop during this survey
occurred at Station 2 where chlorophyll a standing
crop was near maximum (Table 7-1). At Station 3
below the Lima STP, chlorophyll a reached maximum
value, but biomass standing crop exhibited a 40
percent decline from that observed at Station 2. Both
chlorophyll a and biomass progressively declined at
Stations 4 and 5 and then exhibited increases at
Station 6. Chlorophyll a continued to increase at
Station 7, whereas biomass decreased to values near
those observed at Station 1 (reference station).
Chlorophyll a progressively declined at Stations 8 and
9, but biomass standing crop remained at approxi-
mately 20 g/m2.
7.3 Evaluation of Periphytic
Community Response
The apparent responses ofthe periphyton community
to the three principal discharges into the Ottawa
River varied depending on the parameter(s) being
evaluated. For chlorophyll a and biomass data, any
responses (either separate or additive) to the three
discharges need to be evaluated with an under-
standing of the general health of Station 2, located
immediately upstream from the Lima STP. Station 2
as a reference station exhibits effects from some
upstream source associated with the City of Lima.
The greatest biomass and diversity were found at this
station along with a relatively high chlorophyll a
value. Skeletonema, Thalassiosira, and Amphora
were present in greatest abundance at Station 2.
Predominance of certain species of these genera
suggests effects other than nutrient enrichment,
such as organic loading. Adverse effects of discharges
on periphyton often cause large increases in the
Autotrophic Index (Weber 1973; APHA 1981). How-
ever, nutrient enrichment caused by discharges from
waste treatment facilities also are considered effects
altering natural populations. The discharge from the
Lima STP caused a reduction in the AI index,
suggesting that periphytic algae were responding
positively to nutrients contained in the discharge.
Subsequent dilution and depletion of these nutrients
was reflected in progressively increasing AI values at
downstream stations (Stations 4, 5, and 6).
More distinct responses to the discharges were
evident when periphyton abundance, composition,
and diversity were examined. Except for the very high
density at Station 3 and the moderately high density
at Station 6, total periphyton abundance was rela-
tively uniform at Stations 2 through 8 (40,000-
55,000 cells/mm2). However, diversity, equitability,
and periphyton composition fluctuated greatly. Stigeo-
clonium and Nitzschia exhibited the most discernable
response to the discharges; both of these genera have
species considered tolerant of polluted conditions
(Palmer 1977); however, they respond differently to
certain pollutants. The discharge from the Lima STP
caused a drastic increase in the density and relative
abundance of Stigeoclonium, apparently at the
expense of other genera, and diversity plummeted as
a result (Figure 7-2).
Below the discharge from the refinery, Nitzschia and
Stigeoclonium exhibited a reversal of abundance
levels to each other, and diversity approached the
high level observed upstream from the Lima STP.
These patterns suggest a mitigation by the refinery
effluent to the nutrient enrichment imposed by the
Lima STP. However, this mitigation of effects by the
refinery discharge upon the influence of the STP
effluent is considered temporary and localized be-
cause results at Station 5 reflect a return to affected
conditions prior to the refinery discharge. The per-
sistence of effluent constituents (i.e., inorganic
nutrients) from the STP is considered the primary
factor influencing the periphyton rather than a similar
effect from the effluent of the chemical plant because
(1) the contribution of the chemical plant's discharge
to the river flow is inconsequential compared to that
of the Lima STP (Table 6-3), and (2) the chemical
plant's discharge was primarily non-contact cooling
water during the course of the study. Recovery
occurred in a progressive fashion as illustrated in
Figure 7 -2. Nitzschia did not exceed Stigeoclonium in
relative abundance until Station 7, which was
approximately 13 km downstream from the chemical
plant and approximately 5.6 km downstream from the
Shawnee STP. The periphyton community showed
continued recovery at Station 8, and density, composi-
tion, and diversity at Station 9 were as similar to those
at Station 1 as could be expected even for an
unaffected stream over such a long distance (72 km).
In summary, periphyton communities in the Ottawa
River were numerically dominated by either diatoms
or green algae. The green alga Stigeoclonium and the
diatom, Nitzschia, exhibited the greatest response to
the three major discharges. Data on periphyton
7-3
-------
Figure 7-2. Spatial distribution of key periphyton taxa. 1982 survey.
Periphyton
Ottawa River
100
80
60
40
Stigeoclonium
20
~
"0;
c
CD
o
iii
'0
I-
234 5
6
7
8
9
Nitzschia
'0
~ 100
8. 80
'"
~ 60
u
£ 40
20
o Receiving Waters
~STP
fa Refinery
. Chemical Plant
o
Flow.
o
8
9
STP Chemical Plant
Refinerv
Stations
abundance. composition, and diversity were more
useful for evaluating the effects of the discharges
than the chlorophyll a and biomass data, although
these latter data were useful in determining that the
major effect of the Lima STP was probably nutrient
stimulation rather than organic loading or toxicity.
Effluent from the Lima STP produced the greatest
periphyton response. as was expected from the large
volume of this discharge. Some mitigative improve-
ment of conditions is provided temporarily from the
refinery discharge. Uncertainty remains concerning
the effects of discharge from the chemical plant. No
major additive effects of the three principal discharges
were observed. Periphyton at downstream stations
showed substantial recovery toward conditions ex-
isting upstream from the Lima STP Comparison of
the periphytic communities at Stations 7 and 8 did not
indicate nutrient loading from the Shawnee STP
located between the stations to have a similar effect
as that exhibited by the Lima STP.
7-4
-------
8.
Benthic Macroinvertebrate Community, 1982 Survey
The benthic community is considered a good indicator
of ambient response to adverse conditions because of
their general lack of extensive mobility. The degree of
community stability within affected areas can be
measured by comparing composition and dominance
to that of nonaffected areas. An effect on the benthos
would be apparent as an alteration in community
structure, standing crop, or species composition of
the benthos beyond the limits of normal fluctuation
within the receiving waterbody. The increased abun-
dance of nuisance insect larvae or other benthic
species also would be regarded as an effect. The
following discussion is intended to present an
overview of the response of the benthic community
and selected populations to the discharges. Support
benthic data on the composition, relative abundance,
and community parameters are presented in Appen-
dix Tables D-3 and D-4. Methods used for benthos are
discussed in Appendix Section C.2.
8.1 Community Structure
Composition and abundance of benthic invertebrates
varied between stations as summarized in Table 8-1
(based on the 38 most abundant taxa). The community
at Station 1, the upstream reference station (above
the City of Lima) was dominated by the trichopterans
Cheumatopsyche and Hydropsyche, which together
comprised about 43 percent of individuals. The
variety of taxa found at this station were relatively
high; however, total faunal abundance was the
lowest of all stations sampled. Reference Station 2,
which was downstream of the City of Lima but above
the three discharges, had many taxa in common with
Station 1, but had a substantially different community
based on dominance. At Station 2, the chironomid
Cricotopus bicinctus grp. was most abundant, rep-
resenting 31 percent of the individuals in the
community.
A major shift in community dominance was observed
at Station 3, below the Lima Sewage Treatment Plant
(STP) discharge. At this location simuliids (blackflies)
were overwhelmingly dominant. with the larvae (both
unidentified Simuliidae and Simulium) representing
almost 63 percent of the fauna, and the pupae
comprising another 11 percent of the individuals
collected (Table 8-1). The total family thereby ac-
counted for almost three quarters of the community.
The community at Station 4, below the refinery
discharge, was again remarkably different from
Station 3. Community composition shifted back to
dominance by the chironomid C. bicinctus grp.,
although to a greater extent than seen at Station 2. At
Station 4, this taxon comprised 55 percent of the
individuals collected. However, in addition to compo-
sitional shifts, total density of fauna at this station
also dropped dramatically compared to Station 3, and
was similar to that seen at Station 1. Relative
composition of taxa at Station 5, below the chemical
plant discharge was similar to that at Station 4,
except that the dominance of C. bicinctus grp. was
stronger (representing 70 percent of the individuals
collected), and total abundance of individuals was
much greater. The benthic community composition
and dominance at Station 6 was similar to that at
Station 5, although the absolute density of the
dominant chironomid had decreased by about one
third. At Station 7, which was located below the
Shawnee STP, dominance of the benthic community
shifted back to the simuliids as had been observed at
Station 3. The chironomid C. bicinctus grp. was also
relatively abundant at this station. Although Station 7
had many taxa in common with Station 3, individuals
were more evenly distributed among a greater
number of taxa at Station 7. At Stations 8 and 9
community composition tended to be closer to that
observed at Station 1, with dominance by the
trichopterans Cheumatopsyche and Hydropsyche
and an increased abundance of a greater variety of
taxa including the ephemeropterans. However, at
Station 8, the chironomid C. tremulus was the second
most abundant taxa. Also, total faunal abundance
was much greater at Stations 8 and 9 than at Station
1. At Station 9, the abundance of hydropsychids
increased so much that the abundance and distribu-
tion of other taxa decreased compared to Station 8.
Community response was summarized by examining
an index of diversity based on information theory and
a community loss index based on composition.
Diversity and number of species and number of
individuals are graphed by station in Figure 8-1.
Diversity of the benthic community shows a response
to location of the discharges within the study area.
Diversity was greatest (3.895 calculated on log base
2) at reference Station 1, above the City of Lima, and
decreased only slightly at reference Station 2, below
8-1
-------
Table 8-1. Average Denlity (No.lm2) of tha MOlt.Abundant Speciel at Each Sampling Station. Ottawa River. 21 September 1982
Station STA1 STA2 STA3 STA4 STA5 STA6 STA7 STA8 STA9
Number PCT Number PCT Number PCT Number PCT Number PCT Numb"r PCT Number PCT Number PCT Number PCT Number PCT
SpecIes Indlvs Comp Indlvs Camp Indlvs Comp I nd,vs Comp Indlvs Comp Indlvs Comp Ind,vs Comp Indlvs Comp Ind,vs Comp Total Comp
Simuilldae L 1582 022 1 220 40 714 24082 56 62 05 4972 066 1808 007 13560 080 25605 80 64 66 22 60 014 9040 030 5359 62 2459
C (C"cotopUS) B,conctu 1808 025 529970 31 00 1572 96 405 4178 74 55 44 17736 48 7008 1104858 6510 4271 40 1079 696 08 425 1808 006 4857 69 2228
Cheumatopsyche L 171760 211 10 854 28 500 388 72 100 000 000 000 000 000 000 146900 371 437084 26 68 12434 52 41 52 243502 11 17
Hydropsyche. L 1310B 184 000 000 000 000 000 000 904 004 000 000 9040 023 1814781108 7957462657 116101 533
QI ThlenemannlmYla. Grp 21018 295 94016 550 2 17B 64 561 1152 60 15 29 324988 1284 51133 301 85880 217 13334 081 000 000 1041 96 478
~ Hydropsych,dae L 1 360 52 1909 6554 038 5424 014 226 003 000 000 11 30 007 88140 223 2063 38 1 2 59 359792 1201 91372 419
Stenelmls L 339 00 476 178992 1047 110966 286 3390 045 3616 014 000 000 76840 194 668 96 408 2024 96 676 769 45 353
Simuilldae. P 226 003 4520 026 424654 1094 000 000 000 000 000 000 15B 20 040 000 000 000 000 51402 236
C (C"cotopus) Tremulus 2034 029 9040 053 61246 1 58 266 G8 354 000 000 2260 013 29380 074 2660 02 1 6 23 1808 006 455 94 209
Chlronomldae, P 12656 1 78 277 98 163 14238 037 784 22 10 40 1 780 88 704 22600 133 22600 057 16950 103 000 000 423 62 194
Elm,dae. L 17402 244 121136 709 768 40 198 1808 024 1808 007 000 000 22600 057 23730 145 68704 229 38315 176
Baet's. N 770 66 1082 334 48 196 000 000 000 000 3616 014 1130 007 61020 154 18080 110 922 08 308 31877 146
Emp,d,dae. L 1356 019 13786 081 218316 563 452 006 9944 039 000 000 9040 023 9944 061 5424 018 309 83 142
Polypedol um IS S ) Cony, 4520 063 000 000 3616 009 11752 156 280 24 111 406 80 240 768 40 194 300 58 183 18080 060 22101 101
Nanoclad,us. L 904 013 118424 693 4520 012 81 36 108 6554 026 13560 080 6780 017 18306 1 12 1808 006 203 40 093
Caen's. N 12430 1 74 1066 72 624 4746 012 000 000 000 000 000 000 2260 006 363 86 222 000 000 18842 086
Stenelm,s, A 31 64 044 5876 034 72 32 019 000 000 8136 032 2260 013 6780 017 51302 313 61472 205 16792 077
Polyped,lum IS S ) Scala 1130 016 16272 095 4746 012 000 000 000 000 375 73 221 97180 245 1808 011 000 000 15321 070
Bothrooneurum VeJdovskya 248 60 349 228 26 1 34 19210 049 268 94 357 11752 046 000 000 000 000 226 001 21696 072 14821 068
Ephemeroptera, N 393 24 552 9492 056 000 000 000 000 000 000 000 000 293 80 074 15368 094 37968 127 14611 067
IMM Tub,f with Cap Chaet 000 000 000 000 226 001 8136 108 26216 104 91530 539 180BO 046 452 003 000 000 14270 065
IMM Tub,' W 0 Cap Chaet 7006 098 25312 148 000 000 6102 081 171 76 06B 24860 146 2260 006 3616 022 23504 078 12141 056
D'ptera P 2034 029 5876 034 2260 006 16272 216 46104 182 18080 107 2260 006 3842 023 000 000 10774 049
Berosus L 000 000 000 000 000 000 000 000 11752 046 71190 419 203 40 051 000 000 000 000 9881 045
T "clad,da 5876 082 786 48 460 000 000 000 000 000 000 000 000 000 000 000 000 000 000 9828 045
Choronomus, L 000 000 13334 078 226 001 904 012 1808 007 652 50 384 000 000 1808 011 000 000 8173 037
Physella 452 006 000 000 000 000 000 000 20792 082 203 40 120 29380 074 1808 011 000 000 7306 034
Baet,dae, N 12204 1 71 5650 033 000 000 000 000 904 004 000 000 248 60 063 6328 039 9040 030 6281 029
Crocotopus Syvlestros GR 000 000 000 000 000 000 000 000 13786 054 480 25 283 000 000 000 000 000 000 6070 028
Heptagenlldae, N 2712 038 904 005 000 000 000 000 000 000 000 000 000 000 350 30 214 3616 012 4914 023
Rheotanytarsus L 226 003 000 000 000 000 000 000 000 000 000 000 000 000 24182 148 14464 048 4520 021
L,mnodrolus Udekem,anus 000 000 000 000 72 32 019 12656 168 8136 032 22 60 013 000 000 904 006 5424 018 4205 019
Stenacron, N 9492 1 33 000 000 226 001 000 000 000 000 000 000 000 000 24182 148 000 000 3942 018
G Iyptotend'pes L 226 003 5424 032 228 26 059 904 012 000 000 000 000 2260 006 180B 011 000 000 3837 018
Tanytarsus L 6102 086 1808 011 12656 033 000 000 000 000 000 000 22 60 006 9944 061 000 000 3758 017
Hydroptlla, L 000 000 000 000 000 000 000 000 000 000 000 000 33900 086 4294 026 000 000 3653 017
Simulium, L 000 000 000 000 282 50 073 000 000 000 000 000 000 2260 006 000 000 000 000 3495 016
Potamothrlx Bavartcus 000 000 2034 012 000 000 678 009 72 32 029 18080 107 4520 011 000 000 000 000 3259 015
Ot her Spec les 899 48 1262 64410 377 289 28 075 12204 162 24182 096 468 95 276 432 23 109 55144 337 17176 057 423 36 194
Statton Total and
Date Total 7125 78 1 7096 89 3880871 753710 25309 74 16972 60 39598 05 16384 99 29947 26 2179844
Note L = Larva S S = Sensu strictu (In the strIct sense)
P = Pupa A = Adult
N = Nymph
Caprtall2alton 01 taxa 15 due to computerIzed format
-------
Figure 8-1. Spatial patterns of benthic species diversity and components of diversity, Ottawa River, 1982 survey.
Benthos
Ottawa River
4
3
)(
Q) 2
"t:J
.:
Diversity
-- - - Community Loss
r-..-
/ -----------------
60
45
'"
Q)
'u
Q)
c.
en 30
'0
ci
z
15
2345
6
7
STP Chemical Plant
Refi nery
Stations
the City of Lima. However. diversity of the community
below the Lima STP, at Station 3, dropped sub-
stantially, to 1.753. A slight improvement in diversity
occurred at Station 4, below the refinery discharge,
but was caused by a high evenness or relatively few
individuals distributed among relatively few taxa. A
return to the minimum observed diversity was then
seen at Station 5, below the chemical plant dis-
charge. Recovery in terms of community diversity
progressed from Station 6 through 8 with diversity at
Station 8 (3.605) close to that observed at the
upstream reference stations. Diversity at Station 9,
the farthest downstream recovery station, was lower
than that at Station 8.
The community loss index from Courtemanch (1983)
is based on the presence or absence of species and
emphasizes taxonomic differences between the
reference station and the station of comparison. The
- - - No. of Species
- No. of Individuals
o Receiving Waters
IZI STP
If} Refinery
- - - '"'~ Chemical Plant
'-
'-
"'-
'-
40.000
30.000
E
"-
ci
~
.!!!.
ttI
=>
"t:J
:;:
ii
.:
20.000
10.000
'0
~
'iij
c:
Q)
C
Q)
CI
~
Q)
>
«
o
8
9
premise behind the index is that rarer species are
given equal weight to the more abundant taxa.
Therefore, an effect is measured as the elimination of
entire species populations. The formula for commu-
nity loss is as follows:
A-C
=
B
where
A =
B =
number of species found at reference station
number of species found at station of
comparison
number of species common to both stations
C =
As the value increases. the degree of dissimilarity
with the reference station increases. The spatial
trend in the values illustrates a peak in the index at
8-3
-------
Station 4, although the values at Stations 3,5, and 6
are similarly high (Figure 8-1). These data from the
community loss index suggest the greatest effect
upon the benthic community composition occurred at
Station 4 where results of the diversity index indicated
some "false" improvement.
The pattern of diversity is reflected strongly in the
evenness component of the diversity index (Appendix
Table D-4) which considers the way individuals are
distributed among species. Evenness and richness, or
the relative number of species present, are the two
primary components of diversity, while the commu-
nity loss index is influenced solely by the number of
species. In the Ottawa River study area, number of
species dropped substantially at Station 3 (Figure 8-
1), below the Lima STP, and remained low in the
vicinity of all three dischargers (i.e., Stations 3, 4, and
5). Therefore, the effect on the number of species was
consistent among the affected stations. The pattern
of recovery at Station 4, below the refinery discharge,
relative to Stations 3 and 5 is reflected in the
evenness component and can be best understood by
examining number of individuals present (Figure 8-
1 ). At Station 3, despite the drop in number of species,
total abundance of individuals increased substantially
primarily due to an increase in only a few species. The
high dominance of a few species corresponds (by
definition) to a low evenness, and therefore low
diversity. Although number of species remained low
at Station 4, total abundance also dropped back to
levels comparable to reference Station 1 (Figure 8-1 ),
so that the predominance of one or a few species was
not as strong, and evenness and diversity both
increased. As the community loss index suggests, the
composition of the community at Station 4 is dis-
similar from that at Station 1. The pattern described
for Station 3 (i.e., predominant abundance of one or a
few species) reoccurred at Station 5, resulting in a
low evenness component and low diversity. Down-
stream of Station 5 the patterns were more subtle.
Number of species (i.e., richness component) re-
covered from Stations 6 through 8, as did the
evenness component and diversity. Although total
abundance of individuals was high at Station 7, below
the Shawnee STP, predominance by one (or a few)
species was apparently not as strong as at Stations 3
and 5, so that the effect on diversity was small. The
combination of a drop in number of species and a
slight decrease in evenness resulting from an in-
crease in number of individuals was responsible for
the decline in diversity observed at Station 9.
8.2
Spatial Trends in Key Taxa
Certain key taxa represent the greatest contribution
to total abundance of the benthic community evaluat-
ed under diversity and its components. Based on the
results presented in Table 8-1, Simuliidae larvae, the
8-4
midge, C. bicinctus, and the hydropsychids, Cheumato-
psyche and Hydropsyche, were the numerically
dominant taxa and their abundance trends exert the
major apparent effect on the spatial fluctuations in
abundance of the total benthic community.
Simuliidae increase slightly in abundance at Station
2 from the upstream reference station and then reach
maximum abundance at Stations 3 and 7, below each
STP (Figure 8-2). At the intermediate stations be-
tween 3 and 7, abundances were low, never exceed-
ing 140/m2. The overwhelming dominance of simu-
liids in combination with a decrease in number of
species at Station 3 caused a low diversity and is
reflected in the higher redundancy value. This
response was much less at Station 7 because number
of species remained at a level indicative of recovery,
and the remaining individuals were evenly distributed
among other species so that diversity was high
despite the dominance of Simuliidae at that station.
Figure 8-2. Spatial abundance patterns of key benthic taxa,
Ottawa River, 1982 survey.
26
24
22
20
18
~ 16
)( 14
E 12
ci 10
Z 8
6
4
2
Simuliidae Larvae
2345 6
7
8
9
18
16
14
~ 12
)( 10
E 8
.....
~ 6
4
2
C. (Cricotopusj bicinctus grp.
2345 6 7 8 9
14 - Cheumatopsyche
2> 12 on-- Hydropsyche
- 10 -- Early Instar Hydropsychidae
)( 8
E - - -
6 - -
..... - -
o 4
Z
2
2345 6 7 8 9
Stations
-------
Cricotopus bicinctus grp. occurred in maximum
abundance at Station 5 below the chemical plant
discharge and decreased steadily at following down-
stream stations (Figure 8-2). The numerical domi-
nance of C. bicinctus and the low number of species
at Station 5 accounted for low diversity values at that
station. C. bicinctus also showed a secondary abun-
dance peak at Station 2, with a subsequent decline at
Station 3 below the Lima STP
The numerically dominant caddisflies Cheumato-
psyche and Hydropsyche exhibited similar abundance
trends to each other; their spatial distribution indicat-
ed adverse water quality conditions between Lima
STP and Allentown. They dropped in abundance after
the Lima STP and did not increase in numbers until
Station 7 (Figure 8-2). Recovery continued down-
stream where peak densities of both genera were
found at Station 9.
Although the Ephemeroptera constituted a smaller
component of the benthic community than either the
dipterans or trichopterans, the spatial trends in
abundance of the mayflies showed a strong relation-
ship to the location of the discharges, thus depicting
similar trends as other groups. 80th Caenis and
Baetis along with early instar 8aetidae were nearly
absent from Station 3 below the Lima STP discharge,
through Station 6, downstream of all three discharg-
ers (Figure 8-3). Recovery began at Station 7.
Interestingly, Baetis and Caenis showed converse
abundance patterns at stations other than the
discharge stations, which may indicate competitive
interaction between the two genera.
Spatial trends of major benthic groups are plotted for
comparison with those of the key taxa to eva I uate the
relative quantity and quality of information gained
regarding instream effluent effects. Ephemeroptera
and Trichoptera were present in widely different
densities and are plotted on different abundance
scales; however, they underwent similar abundance
trends relative to location of the plant effluents, being
nearly depleted from the stations nearfield to the
dischargers (Figure 8-4). The spatial fluctuations of
both of these groups are reflective of the key taxa
within those groups. Therefore, comparable infer-
ences of community response would be drawn from
examination of these two major taxonomic groups as
from examination of component species. The Chiron-
omidae and Oligochaeta, also graphed on different
density scales from each other both depict a some-
what different response to the dischargers than that
of the ephemeropterans and trichopterans (Figure 8-
4). 80th the midges and worms decrease in abun-
dance immediately after the Lima STP(Station 3), and
then begin to increase in abundance, with Chiron-
omidae peaking at Station 5 and Oligochaeta at
Station 6. 80th gr()ups then undergo a decrease in
abundance downstraam with the exception of a rise
Figure 8-3. Spatial abundance patterns of the dominant
ephemeropterans. Ottawa River. 1982 survey.
1,000
900
800
700
E 600
ci 500
Z 400
300
200
100
- Baetls SDP
.u Early Instar Baetidae
\
\
/~~--- ;/
( --- /
t' ---'--. /.-
2345 6
7
8
9
1,100
1,000
900
800
E 700
:; 600
Z 500
400
300
200
100
f C",;, 'P'
/'
.../
2345 6 7 8 9
Stations
in abundance for the Oligochaeta at Station 9. This
pattern suggests an opportunistic response (i.e.,
increase in abundance) to stressed conditions be-
ginning below the City of Lima (Station 2) and
continuing more strongly in the vicinity of the
discharges, with this pattern interrupted by an
apparent toxic response after the Lima STP (Station
3).
The spatial trend in total Chironomidae matches the
spatial trend of C. bicinctus, so that interpretation
based on the total group would be similar to that for
the dominant component species. However, the
spatial trend in abundance of Oligochaeta is due to
several species influencing total abundance. Bothrio-
neurum vejdovskyanum is a primary contributor to
the peak densities of worms at Stations 1,2,4, and 9.
The maximum peak of worms found at Station 6 is
due to a normally uncommon species, Potamothrix
bavaricus (including immature forms) which was not
abundant at the reference and furthest downstream
station (Table 8-1). Species of Limnodrilus also
contribute to peaks at Stations 4,5, and 9, but are not
abundant at the intermediate stations. In this case,
component species respond variously, not only to
location of the discharges, but also to related and
interactive factors such as competition, predation,
food availability, and microhabitat characteristics.
8-5
-------
Figure 8-4. Spatial distribution of major benthic groups.
1982 survey.
Benthos
Ottawa River
2,000
- Ephemeroptera
-- -. Oligochaeta
1,500
E
ci 1,000
z
500
\.. -- .... .... ...
----......"",,"'--
2345 6
7
8
24
22
20
18
(, 16
14
>C
E 12
...... 10
ci 8
z
6
4
2
- Chironomidae
--- Tnchoptera
,
/
/
/
/
/
/
/
,,/
'"
8
5tatlons
8.3 Benthic and Zooplankton Drift Col-
lections
Density estimates averaged over replicates. for each
of the four drift collection stations. is presented in
Table 8-2. These taxa represent five major taxonomic
groups: aquatic insects. zooplankters. gastropods.
annelids. and (non-zooplanktonic) arthropods. Sever-
al minor taxa (e.g.. Turbellaria and Hydrozoa) were
also represented. Of the taxa encountered. the
aquatic insects were the most abundant, with the
chironomid larvae and dipteran pupae (most of which
are chironomid pupae) being numerically dominant.
Chironomid larvae and pupae. together. constituted
approximately 86 percent of the total number of
individuals collected.
Density comparisons across stations indicate that the
lowest total abundance of organisms occurred at
Stations 2 and 3 (Table 8-2). Density increased at
Station 4 and peaked at Station 5, with an average of
5,414/100 mJ The greater densities at Stations 4
and 5 were attributable in part to the greater
abundances of chironomid larvae and pupae at these
stations compared to the reference Station (2) and the
8-6
Table 8-2.
Density (No.l100 m3) of Macroinvertebrates
Collected from the Drift. Ottawa River. 23
September 1982
Station
.,
If
Macroonvertebrate 2 3 4 5 Average
Hydrozoa 1.24 0.56 0.45
Trtcladida 301 29.07 8.02
Gastropoda 8.96 224
Ancylidae 5.52 1.38
Physella 0.34 0.62 23.34 6.08
Tubif,cldae 11.22 3.17 3.60
Na.dldae 16.44 9.61 72.97 5.51 26.13
Branch.obdellidae 53.27 0.30 13.39
Acartna 2.22 0.56
Cladocera 161 7.37 0.61 2.40
Ostracoda 0.38 0.10
Cyclopo,da 3026 5.66 128.02 450.64 153.64
Calanolda 1.34 0.34
Isopoda 0.52 0.13
Astacidae 1.40 0.86 0.56
Orconectes 0.30 1.06 0.34
Unod Insect 1.03 0.26
Collembola 0.52 0.30 159 0.60
Ephemeroptera N 0.38 5.82 1.55
Caenls N. 8.12 231 1.49 1.59 3.38
Baetls N 1.40 12.45 3.46
Heptagenlldae N 3.70 0.92
lygoptera N 0.62 0.16
Coenagrton,dae N. 1.22 170 0.73
Arg,a N 159 0.40
Calopteryx N 0.52 0.13
Cortxldae A. 0.30 0.52 0.20
Gerrodae, Imm 0.52 0.13
Hydropsychldae L. 3.70 0.77 1.12
Coleoptera L. 2.80 0.56 0.84
Elm.dae L. 5.11 0.77 1.47
Elm,dae A 4.32 1.08
Stenelmis L 0.30 0.08
Stenelm,s A 1.85 5.31 1.79
Dub"aph,a L 0.38 0.10
Hal.phdae A 1.18 0.30
Dyt,sc,dae A. 0.52 0.13
Dlptera L 1.85 0.52 0.59
Dlptera P 7370 95.05 484 28 3,851.361,126.10
S,muilldae L. 1962 34.79 5.42 14.96
S,muilldae P. 0.38 0.10
Emp,d,dae L. 128 0.56 170 0.88
Emp,d,dae P 0.38 0.10
Ch,ronom,dae L. 143.22 95.12 411.76 1,019.11 417.30
Psychodidae L. 0.62 0.52 0.28
STP influenced Station (3). Community diversity, in
terms of the number of species present, was greatest
at Station 5 where 29 taxa were identified and lowest
at Station 2 where only 17 taxa were collected. The
additional taxa at Station 5 (and also Station 4) were
insects. primarily dipterans. odonates, and hemipter-
ans, which were lacking at Stations 2 and 3.
The densities of the predominant taxa in the drift from
each station reflected the dominance of the benthic
populations at those stations which indicates that
drift as a dispersal mechanism is heavily dependent
upon localized drifting. The greatest density of
simuliid larvae in the drift occurred at Station 3 where
the largest population in the benthos was found;
simuliids were completely absent in the drift from
Station 5 where, again, they were rare in the benthos.
Approximately 82 percent of the dipteran pupae and
78 percent of the chironomid larvae encountered
were from Station 5, where they were more abundant
-------
in the benthos than at the other stations sampled for
drift.
Although ephemeropterans were relatively minor
components of the drift in terms of abundance
contribution, individuals of this insect order were
present at all four stations indicating that colonization
potential of this group is not entirely eliminated from
the affected area where the benthic populations of
this group are not abundant. None of the insects other
than Chironomidae were abundant in the drift at any
station. However, more insect orders were repre-
sented at Stations 3, 4, and 5 compared to the
reference Station (2). The converse was true for the
benthic population; that is, more insect orders were
present at Station 2 compared to the downstream
stations.
The relative population contribution of major benthic
taxa was compared among stations to ascertain
Figure 8-5. Spatial trends of proportion (percentage) of
population in drift compared to benthic standing
crop for major taxonomic groups. 1982 survey.
100
Chironomidae Pupae
50.0
40.0
30.0
"
20.0
,
,
,
,
,
"
,
,
I
,
I
,/ Ephemeroptera In drift
... - but not in benthos
,
I
,
,
I
,
,
,
I
I
I
I
I
I
I Ephemeroptera
I
I
I
I
I
I
'"
,"-
I "-
, "Trichoptera
: "-
"
"-
"
10.0
I/)
CI>
C>
~ 5.0
CI>
Q" 4.0
CI> 3.0
(ij
2.0
o
...J
1.0
0.5
0.4
0.3
0.2
0.1
2
3
Stations
4
5
whether a relationship between standing crop and
drift abundance would show informative spatial
trends. Differences of relative proportions within
groups among stations might suggest adverse envi-
ronmental pressures resulting in population instabil-
ity. An index of proportioning population abundances
in the drift was obtained simply by calculating the
ratio of drift density to benthic density. A plot of these
indices (percent) illustrates the spatial trend of the
chironomid larvae and pupae, ephemeropterans, and
trichopterans (Figure 8-5). The standing crop-drift
relation indices indicated that drifting of chironomid
larvae and pupae and ephemeropterans increased
downstream through the affected area. Sampling
constraints, such as varying time of collection at each
station for drifting organisms which exhibit distinct
diel periodicity, may have had some influence on
spatial differences. However, increasingly adverse
water quality conditions from upstream to down-
stream could also influence higher drift proportions.
Drifting of the trichopterans steadily decreased in
direct proportion to the community from upstream to
downstrea m. Neither drifti ng trichoptera ns nor those
in the benthos were found at Station 5.
Very little information on zooplankton drift was
gained from this study primarily because of the large
mesh (500 JIm) of the nets used in the survey.
However, cyclopoid copepods were an abundant
component of the drift and exhibited a decrease in
density from Station 2 (30/100 m3) to minimal
abundance at Station 3 (6/100 m3), and then
increased to relatively large abundances of 128/100
m3 at Station 4 and 450/100 m3 at Station 5 (Table
8-2). Other zooplankton components were not abun-
dant in the drift collections with 500-Jlm mesh nets.
Evaluation of the Macroinvertebrate
Community
The sampling design for the 1982 survey was taken
from previous surveys (Martin et al. 1979; Engineering-
Science 1981) so that direct comparisons of spatial
community trends could be related among the three
studies. The findings of the present study supported
degradation of the benthic community from the Lima
STP to the Allentown Dam, where initial recovery of
the benthic community was noted. These findings are
similar to those found in the Ohio EPA study (Martin
et al. 1979). The health of the community improved
downstream of Allentown. However, station-specific
intricacies of the composition and diversity of the
benthic community need to be evaluated using know-
ledge of specific organism sensitivity and ecology to
better understand the effects imposed by the dis-
charges.
A major shift in the benthic community structure
occurred below the Lima STP discharge from that at
8.4
8-7
-------
the upstream reference station as reflected in an
abrupt drop in diversity and number of species and a
substantial increase in abundance of Simuliidae
(blackflies). The reduction in number of species at
Station 3 was primarily due to an absence of many
insects other than dipterans and coleopterans. The
trichopterans and ephemeropterans, which consti-
tute the more important insects within this group,
were noticeably lacking from Station 3. Although
species within these two insect orders exhibit a wide
variation in tolerance to adverse water quality
conditions (Harris and Lawrence 1978; Hubbard and
Peters 1978), each species is generally restricted to a
finite range of water quality conditions. The distinct
absence of the caddisflies and mayflies from below
the Lima STP suggests a relatively high level of
intolerance to the effluent constituents of the STP
Simuliid larvae are filter feeders and feed upon
nutrients and planktonic organisms flowing past their
places of attachment (Davies et al. 1962; Stone
1964). Some species of Simulium are very tolerant of
organic pollution (Hilsenhoff 1981). The overwhelm-
ing dominance of Simuliidae at Station 3 suggests an
area of nutrient enrichment which is limiting to other
less facultative organisms.
A slight rise in the diversity index at Statibn 4 located
between the refinery and chemical plant discharges
reflected a compositional shift in the community. A
high evenness value supported by a decrease in the
number of species and benthic abundance at Station
4 from that observed at Station 3 influenced the
diversity index (Figure 8-1). The abrupt decrease of
simuliids from peak density at Station 3 to minimum
abundance at Station 4 supports some alteration of
the effects of the Lima STP by the refinery discharge.
The community loss index suggested that the compo-
sition of the community was dissimilar to that of
Station 1. This alteration of the community at Station
4 does not reflect recovery from effects of the Lima
STP. The results from the drift collections indicated
that drifting is relatively localized and successful
colonization from an upstream source population is
not occurring. Insufficient data exist to asess the
effects upon the survival or propagation of those
populations experiencing effluent plume entrainment
during drifting period.
Engineering-Science (1981) found inconsistent spa-
tial abundance trends in their zooplankton drift data
among seasons, even though zooplankton abun-
dances were higher below the Lima STP than above
in September of 1979 which corresponds to the
month of our collection. No attempt was made by
Engineering-Science to separate out the component
taxa so a direct comparison to our data is not
warranted. Results of zooplankton data from the
present study's drift collections suggest that the
cyclopoid copepods, which are the numerically domi-
8-8
nant macrozooplankton component, are not able to
maximize population potential until after the refinery
discharge.
The benthic community exhibited stressed conditions
at Stations 5 and 6 located 3.4 and 8.0 km down-
stream, respectively, from the Lima STP However,
the community dominants were different at these two
stations. Cricotopus bicinctus, a midge larva, domi-
nated the fauna at Station 5, while Potamothrix
bavaricus, a tubificid worm, dominated at Station 6.
This difference in benthic structure may have been
more influenced by subtle habitat differences than by
variations in water quality. The habitat at Station 6
was characterized by extensive algal mats attached to
the substrate. Also, more sediment was sampled at
Station 6 allowing for a more complete sampling of
infauna than at Station 5 where a rockier substrate
was present. Most species of Cricotopus are con-
sidered saproxenous (tolerant of slightly polluted
waters) (Beck 1977) and their presence is not
surprising; however, the specific reason for their
dominance at Station 5 is not clear. P. bavaricus,
although a relatively uncommon species of worm, is
found in various river systems in the United States
(Spencer 1978). Not much is known of their water
quality requirements, and their dominance at Station
6 is unexplained.
A recovery of the community at the Allentown Dam is
exemplified by the return of the trichopterans and
ephemeropterans along with other insects. It should
be noted that the abundance of Simuliidae increased
at this station (Station 7) to a level above that
collected at Station 3. The proximity of the Shawnee
STP upstream from Station 7 is most likely the reason
for this increase. In comparison of effects, both STPs
(Lima and Shawnee) apparently contribute nutrient
enrichment to the receiving waters; however, toxicity
to the benthic community is not present in the
Shawnee STP effluent as is apparent from the
relative stability of the benthic community at the
Allentown Dam.
Comparison of the spatial trends in abundance of the
major groups and the key taxa indicate that similar
results and conclusions are obtained when the major
groups examined are dominated by relatively few
taxa. Information is lost in relying on major groups in
terms of diversity indices and associated components,
which are based on the number of taxa and distribu-
tion of individuals among the taxa. It should be
emphasized that examining trends of major benthic
groups should be at the lowest possible level (family
taxonomic level) in order to retain as much informa-
tion on composition shifts as possible for correct
interpretation of effects.
In summary, effects on the benthos are primarily due
to the Lima STP Some alteration of the benthic
-------
community occurs below the refinery discharge, but
not enough for recovery of the community. Coloniza-
tion potential from drifting is low in the area below the
Lima STP Recovery of the benthic community was
determined to occur at Allentown located approxi-
mately 14 km downstream from the Lima STP. Some
nutrient enrichment may occur at Allentown due to
the Shawnee STP, but no ambient community
response to toxicity was determined.
8-9
-------
9.
Fish Community, 1982 Survey
Table 9-1. Results of Fisheries Survey of OUawa River, Abundance by Station, 24-26 September 1982
Station
1 " 2" 3" 4 5 6 7 8
Gizzard shad
Carp 2
Cyprinidae (small)
Golden shiner 20 5 1 1
Fathead minnow 38 1 15 6 2 50
Creek chub 4 21 81 5 1 242
Spotfln shiner 29
Emerald shiner 1 1
Bluntnose minnow 130 98 10 2 4 1,249
Stoneroller 16 2 3
Sand shiner 3
Redfin shiner 1,098 3,227 3.430 2 3 26
Notropis sp. 444 3
White sucker 36
Black red horse 16
Golden red horse 2
White catfish
Tadpole madtom
Blackstrlpe topmlnnow
Rock bass 2
Green sunfish 118 25 2 2 3
Bluegill 10 227 23 1 3
Largemouth bass 1 19 3
Black crappie 5
Lepomls sp 4
Lepomis x Lepomis hybrid 9
Greenslde darter 23 6
Rainbow darter 22
Fantail darter 16 2
Johnny darter 28
Blackside darter
No. of species 13 15 11 6 3 0 8 11
"Aliquot procedures used.
"Qualitative sample separate from standard unit of effort.
9-1
The fish community is the highest trophic level to be
potentially affected by polluted discharges. It ultimate-
ly represents the major concern as a sport fishing
resource and reflects the environmental health of the
stream. The following discussion is intended to be an
overview of the response of the fisheries community
to the selected discharges. Support data to this study
are included in Appendix Tables D-5 and D-6. The
fisheries methods are detailed in Section C.3.
9.1 Community Structure
The fisheries collections in the Ottawa River yielded
27 species, one hybrid, and three taxa of fish that
could only be identified to the family or genus level
due to their small size (Table 9-1). In total, seven
families were represented. The most widely distri-
buted fish were the fathead and bluntnose minnows,
creek chub, and redfin shiner, which were collected
at seven of the nine stations. The green sunfish and
bluegill were each caught at six stations.
At the reference station (Station 1) above the City of
Lima, 12 species representing four families were
caught, with redfin shiner dominating the catch. An
abundance of young-of-the-year or juvenile shiners
(Notropis) were found. Four species of darters also
were found to be common.
Station 2 was located below Lima, but above the three
discharges examined in this study. Fifteen species
from four families were found at this station. The
9
2
121
4
4
227
32
319
8
42
6
1
10
2
2
2
2
(3)"
1
1
18
-------
darters were much more poorly represented both in
numbers and diversity than at Station 1, whereas
minnows, particularly the redfin shiner ar'!d sunfish
predominated.
The general abundance and number of species
captured remained high at Station 3, located just
below the Lima Sewage Treatment Plant (STP)
discharge; however, the presence of darters was
reduced to only one specimen of rainbow darter.
Suckers, on the other hand. appeared in moderate
numbers compared to the two reference stations.
General abundance and diversity were further re-
duced below the refinery outfall at Station 4. Only 26
fish from three families were found at this station.
Three species totaling 10 fish were caught at Station
5, downstream from the chemical plant discharge.
Several species of minnows and the green sunfish
were the predominant fish at both stations. No fish
were caught at Station 6, located approximately 6 km
downstream of the refinery discharge. This station
was heavily fouled with filamentous algae.
The minnow family predominated at the stations
farther downstream. Sunfish reappeared but in low
numbers. A total of 19 fish from seven species were
caught at Station 7, indicating some recovery, despite
low DO levels. Nine species of minnows totaling
1.610 fish plus three green sunfish were caught at
Station 8.
At Station 9, approximately 58 km downstream from
the three discharges, species variety had risen back to
levels found at Stations 1 and 2 with a greater
number of families represented at this furthest
downstream station. Darters once again appeared
here, although in very low numbers with only one
Johnny darter and one blackside darter caught. Three
additional greenside darters were found in a quali-
tative sample outside the station collection effort.
The Shannon-Wiener diversity index and the com-
munity loss index were performed on the catch data
from the fisheries survey at Ottawa River. Diversity
increased at Stations 4 and 5 to a level comparable to
the reference station (Station 1). These results could
be misleading in suggesting recovery of the fish
community in this area. However, the high diversity
values were due to high evenness and low redun-
dancy, or, as illustrated by number of species and
abundance (Figure 9-1), few individuals being distri-
buted among few species. Diversity decreased at
Station 3 from that observed at the reference stations.
Although abundance remained high at 3, the number
of species decreased resulting in this lowered divers-
ity. The combination of these data suggests that some
alteration of the fish community below the STP has
occurred.
9-2
The community loss index showed a strong dissimilar-
ity between the communities at the influenced
stations of 4,5, and 6 to that of the reference station
(Figure 9-1). These results supported the conclusions
derived by the trend in the diversity index in that the
fish community was apparently most affected by the
refinery discharge. Any direct effects from the STP on
the fish community is subtle and minimal in compari-
son to the community changes noted below the
refinery.
The salient trends in spatial distribution are illustrated
by the major components of the fish community
(Figure 9-2). Two species of minnows account for the
largest proportion of fish abundance at the sampling
stations. The redfin shiner was most abundant and
numerically dominant upstream from the refinery
discharge. The redfin shiner was not abundant
downstream of the refinery and had not returned to
former abundance levels noted at reference areas by
Kalida. Conversely, the bluntnose minnow was not
abundant above the refinery, but became numerically
dominant at Stations 8 (Rimer) and 9 (Kalida).
The substantial decrease in the presence of darters
from the reference area above Lima to the affected
area had a considerable influence on the number of
species at each station (Figure 9-2). Four species of
darters comprising 89 individuals were found above
Lima. The darter population appeared to be affected
prior to the STP and never recovered until Kalida
where only three species in low abundance were
collected. One of the species, the blackside darter,
was found at no other station. Centrarchids also had a
major influence on the spatial trend of species
numbers (Table 9-1) which declined steadily from 15
species at Station 2 above the STP to zero at Station 6
(Figure 9-2) approximately 5 mi downstream from
Station 2. The variety of fish was restored partially at
Station 7 (below Allentown Dam) and increased to
maximum levels (18 species) at Kalida, the furthest
downstream station.
9.2 Evaluation of Fish Community
Response
Fish collections were made on the Ottawa River
during 1976 and 1977 by the Ohio Environmental
Protection Ag'ency as part of a water quality study
(Martin et al. 1979). The methods used in the EPA
study were qualitative in nature, but the results can
be used to compare trends in the fish communities
found in this study. Collections were made by Ohio
EPA at Stations 1,2,4,7,8, and 9 plus several others
not sampled during our study.
Due to the greater intensity of the Ohio EPA's
sampling efforts, more species were found than in the
present survey. Most notably, EPA encountered the
grass pickerel (Esox americanus vermicu/atus) at
-------
Figure 9-1.
Spatial distribution of fish community indices and associated parameters, 1982 survey.
4
(12)
X
/ \
I \
I \
I
Fish
Ottawa River
- Diversity
-- Community Loss
- No. of Individuals
-- Number of Species ./
o Receiving Waters /" ./
~ STP ./'
~ ' ./'
~ Refinery ./'
. Chemical Plant ./'./'
--'"
--
--
--
/
/
/
/
3
)(
CD
-g 2
2 345
6
7
20
15
(/)
CD
'u
~ 10
en
'0
"-
CD
.c
g 5
z
o
Flow
STP Chemical Plant
Refinery
several stations, whereas no esocids were collected
in the present study. Except for three species and one
hybrid, all of the fish collected by EPA had been
encountered previously in the Ottawa River by Ohio
EPA or Trautman (1957) and Patrick et al. (1956) as
summarized in Martin et al. (1979).
In 1976 and 1977, Station 1 was found to have a
healthy community of fish. Although the grass
pickerel, blackstripe topminnow, and the sucker
family which were caught in 1976 and 1977, were
not well represented in the present study, the
abundance of other fish, especially the darters,
indicates that Station 1 has not become more de-
graded since EPA's study. Station 2, sampled previ-
ously in 1977, was characterized as a stressed
ecosystem by EPA because there was low species
---
----- --
---
8
9
40.000
30.000 0
~
:J
!!?
:<
Z
20,000 0
~
m
UI
3~
10.000
9
Stations
diversity and pollution-tolerant species were present.
In the present study, a slightly better species diversity
was found with a greater abundance of bluntnose
minnow, redfin shiner, bluegill, and largemouth bass,
plus two species of darter. Species composition at
Station 4, located between the refinery and the
chemical plant, was similar to that of the 1976 and
1977 studies with mainly fathead minnows, creek
chubs, and green sunfish caught. Ohio EPA found the
section of the Ottawa River between the chemical
plant outfall and the Allentown dam to be "essentially
devoid of fish populations" and located no stations in
that section. EPA's Station 5, just downstream from
the discharge of the chemical plant, comprised a poor
fish community of only three species. No fish were
caught at Station 6, located nearly 5 km downstream
from Station 5.
9-3
-------
Figure 9.2. Spatial distribution of selected fish species and
community parameters. 1982 survey.
Fish
Ottawa River
18
~16 ..
'g 14 \
~12
'010
~ 8
1! 6
~ 4
z 2.
-Number of Species
-- Darters (Abundance)
901 ;:;-
80 E
70 :g
60 ~
50 ci
40 ~
30 .~
20 r!
10 I~
------
2345 6 7
9
8
4.000
CD 3.500
~ '3.000
~ 2.500
5 2.000
~ 1.500
1.000
500
- Total Fish Abundance
- - Redfin Shiner
....... Bluntnose Minnow
-----
8
9
Stations
Station 7 showed low diversity during both the Ohio
EPA and the present studies; however, carp, white
suckers, and several sunfish predominated in 1977.
whereas six species of minnow and the bluegill
comprised the 1982 species list. As this station may
represent early stages of recovery, the fish community
may be in a constant state of flux as fish move
upstream from more healthy sections.
The number of species has decreased from 14 to 10 at
Station 8, and the number of families represented
dropped from four to two. However, these data
comparisons are not adequate to properly judge a
change in the general health between 1977 and the
present study. No darters were captured in either
st udy.
In both studies, the number of species collected at
Station 9 returned to levels found at the upstream
control station, but with reduced numbers and
diversity of darters. Ohio EPA considered the presence
of the greenside darter, the logperch (Percina
caprodes), and the blackside darter as demonstrating
that marked improvement had occurred in water
quality. One blackside and three greenside darters
were caught (the greenside darter in an additional
qualitative sample) at this station in 1982, suggesting
no marked change in water quality since 1977 and
recovery from upstream discharge effects is apparent
at this station.
9-4
The condition of the Ottawa River just above the first
of the three discharges appears to be healthy, based
on the abundance of fish and number of species
collected at Station 2. However, the reduced popu-
lation of pollution-sensitive darters may indicate
some degradation caused by the City of Lima or other
point-source discharges. The effluent from the STP
appeared to not substantially affect the fish commun-
ity except for the virtual elimination of the darters.
The effluent from the refinery apparently has had
greater adverse effects upon the fish community in
that the abundance and variety of fishes are greatly
reduced at Stations 4 and 5 compared to that found
upstream.
The total absence of fish at Station 6, located over 5
km downstream from the total discharge, suggests a
delayed effect such as a high 80D. Lethally low
dissolved oxygen levels could occur at night, even
though acceptable levels of 5.7 and 6.8 mg/liter were
recorded during benthos and fisheries collections.
respectively, around midday.
It does not appear that the variable proportions of pool
and riffle habitats among the stations can be corre-
lated to the differences in fish communities. Major
differences in the fish communities were found
within each of two groups of stations where habitat
proportions were similar. (These groups consisted of
Stations 2, 4, 6, and 9 and Stations 3, 5, and 7). In
addition, Station 1 contained the smallest percentage
of riffle habitat, yet produced the greatest abundance
and diversity of darters, which are generally a riffle-
dwelling species. Conversely, no darters were caught
at Station 8, which had a very large proportion of riffle
habitat.
Recovery of the fish community appeared to occur in
stages with distance downstream. The minnow
component appeared to return to normal population
levels (as illustrated by the reference stations) at
Station 8 located approximately 34.5 km downstream
of the refinery outfall, although the dominance of the
minnows shifted from redfin shiners upstream of the
refinery to bluntnose minnows below the refinery.
The darters, on the other hand, did not reach recovery
until Station 9 which is 58.5 km downstream from the
refinery. Recovery of the darters was exemplified
more by variety than abundance. However, the
character of the habitat at this furthest downstream
station was fairly dissimilar to that of the reference
station because of greater flows and sources of input,
and total recovery of darters to population levels
observed at the reference station may not be possible
beca use of their habitat preference for shallow-water
riffle areas.
-------
10.
Fish Caging Study, 1982 Survey
An in situ caging experiment was carried out at six
stations on the Ottawa River. Station 1 at Thayer
Road was the reference station free from influence
from Lima, and Station 2 before Sewage Treatment
Plant (STP) was used to identify any effects from
runoff and discharges from the City of Lima. One
station was located in each of the three discharges
examined: the STP(Station 3), the refinery (Station 4),
and the chemical plant (Station 5). Station 9 at Kalida,
Ohio, was located approximately 60 km downstream
from the three discharges to observe recovery.
10.1 In Situ Toxicity Testing
The greatest mortalities occurred at the three dis-
charge stations, where 50 percent of the test
population or greater died after six days (Table 10-1 ).
The refinery discharge was the most toxic, with only
30 percent surviving. The greatest rates of mortality
at the discharge stations occurred after two days of
exposure (Figure 10-1). As shown by the dye study
conducted at the chemical plant (Figure 6-4), the
cages at Station 5 were not within the discharge
plume of the chemical plant. The mortality here
possibly can be attributed to a diluted refinery
discharge, or a combination of STP and refinery
discharges.
The greatest 6-day survival (85 percent) was observed
at Station 2, just upstream from the STP. A survival of
78 percent occurred at Station 9 (Kalida), indicating
substantial recovery. The mortality rates at these two
stations were fairly constant over the six days of the
study.
The poor survival at the upstream control station
(Station 1, Thayer Road) raises some questlon as to
the validity of this testing. One possible explanation
Table 10-1.
Results of Fish Caging Study, Ottawa River, 1982 Survey
Number of Fish Surviving per Cage
Station Day 0 Day 1 Day 2 Day 3 Day 4 Day 5 Day 6
1A 10 9 9 9 9 8 8
18 10 7 6 5 5 5 5
1C 10 6 6 6 6 6 5
- - - - - -
Total % Survival 73 70 67 67 63 60
2A 10 9 9 9 9 9 8
2B"
2C 10 10 10 10 9 9 9
- - - - - -
Total % Survival 95 95 95 90 90 85
3A 10 10 9 8 6 6 6
3B 10 10 10 9 9 5 5
3C 10 8 7 5 5 4 4
- - - - - -
Total % Survival 93 87 73 67 50 50
4A 10 10 20 4 4 4 4
4B 10 10 9 4 3 2 2
4C"
Total % Survival 100 95 40 35 30 30
5A 10 10 9 7 6 5 4
58 10 9 9 5 5 5 4
5C 10 10 8 7 7 4 3
- - - - - -
Total % Survival 97 87 63 60 47 37
9A 10 10 8 7 5 5 5
98 8 8 8 8 7 7 7
9C 10 10 10 10 10 10 10
Total % Survival - - - - - -
100 93 89 79 79 79
"Missing cages.
10-1
-------
Figure 10-1. Results of in :situ fish caging study, Ottawa River,
1982 survey.
100
80
~60
iO
>
.~
::I
en 40
20
o
o
~''Z~~?;:~~'\\~.--..~._...n''''''''''--_......_--_n...--"-'"
'.\ .................
'" ".
", "
\\ "
\ \ "-'-
--
-""'"
Station 2
Station 9
-.-.-..---- - -- - u-
\ \
\ ----, ".
\ ..... ,
. " .
\ ..... '.
\ ,------
\ "
. ....
. ....
...-------------------------==
Station 1
Station 3
Station 5
Station 4
2
3
Day
4
5
6
for the high mortality is that the increased stress of
transportation in the holding tank may have elimi-
nated the weaker fish and allowed the hardier
individuals to be placed in cages at other stations.
This is supported by the fact that the greatest rate of
mortality at Station 1 occurred during the first day,
after which it was similar to that at Stations 2 and 9.
These results emphasize the need for further testing
and development of these methods.
10-2
-------
".
Benthic Macroinvertebrate Community, 1983 Survey
Both qualitative and quantitative collections were
taken during the 19B3 survey of the Ottawa River,
thus increasing the number of habitats sampled at
each station. Quantitative collections were taken in
riffle areas as in the 1982 survey. Qualitative
collections were taken along shore zones and pool
areas.
11.1 Community Structure
The number of taxa collected at each station ranged
from 12 to 31 (Table 11-1). The largest variety of taxa
were the chironomids which were represented at
each station by several genera. The benthic commun-
ity at Station 8 comprised the most taxa (31) of any
station, having a greater variety of caddisflies,
molluscs, and beetles than the other stations. The
benthic community at Stations 4 and 5 was the least
diverse, having relatively few taxa other than chirono-
mid larvae.
Abundance distribution of the benthos exhibited
somewhat different information on spatial trends
than did composition. The benthic community was
least abundant at Station 2 which is the reference
station (Table 11-2). The greatest abundance was at
Station 7, with over 12,000 organisms/m2. The
difference in abundances was primarily due to the
simuliids and, to a lesser extent, chironomids.
The community loss index as described in Section 8.1
was calculated on the data obtained in the 1983
survey. Two separate indices were calculated and are
based either on total taxa encountered in all sampling
efforts (Table 11-1) or in the quantitative collections
only (Table 11-2). The community loss index indicated
that station dissimilarity to the reference station
(Station 2 was used as the reference station of
comparison in 1983 as opposed to Station 1 which
was used in 1982) increased from a minimum at
Station 3 to a maximum at Station 5, then decreased
until Station 8 (Figure 11-1). Stations 4,5, and 6 were
the most dissimilar to Station 2 in composition. Very
little difference in values was obtained when the
qualitative sampling effort was included in the
calculations.
The spatial trend illustrated by the community loss
index was reflected by the trend in number of species
(Figure 11-1). As the community loss index increased
Figure 11 -1. Spatial trends of benthic community parameters.
1983.
Community Loss Index
1.00 Based on quantitative
- sampling only
Based on total
--- effort
0.80
0.70
0.60
~ 0.50
"'C
E 0.40
0.30
0.20
0.10
. .
/
2
3
6
4
5
7
8
45
12,000 - Abundance (quant.)
--- No. of species (quant. only)
-- No. of species (total effort)
_10,000
E
ci 8,000
z
Q)
g I 6,000
'"
"'C
c:
E 4,000
-------
Table"-'.
Composition of the Benthic Community of the
Ottawa River. July '983
Station
Taxa
Coleoptera
Psephenus L.
Stenelmis L.
Stenelmis A.
Dytlscldae
Agabetes L.
Dytiscus L.
Laccophilus A.
Hydrophilidae L.
Berosus L.
Berosus A.
Peltodytes A.
Ephemeroptera
Baetls
Caems
Stenonema
Trlchoptera
Cheumatopsyche
Hydropsyche
Hydropsychidae P.
Hydroptilidae L.
Hydroptllidae P.
Simuliidae
Simulium L.
Simulium P
Chlronomldae
Pupae
Procladius
Ablabesmyia X
Chironomus 0
C. (Dicrotendipes) X
C. (Cryptochlfonomus) X
C. (Tribelos) X
Glyptotendipes X
Polypedilum X
Stictochironomus
Tanytarsus
Zavrelia
Cricotopus
Psectrocladius
Oligochaeta
Miscellaneous
Hetaerma
Argia
Turbe'laria
Hirudinea
Procambarus
Hyallela azteca
COrlxldae
Gastropoda (snail)
Ancylidae
Hemerodromia L.
Hemerodromia P
Ceratopogonldae L.
Ceratopogonidae P
Tabanidae L.
Chaoborus
Other
Total no taxa"
w/qual
Community Loss Index
(qual & quant.) 025 057 1.00 070 0.35 0.16
"Multiple life stages. higher taxonomic levels. and Oligochaeta are
not Included In number of taxa.
Note 0 = presence of species In quantitative samples only.
X = presence of species In qualitative samples (may Include
quantitative samples).
2
3
4
5
6
7
X
X
X
X
o
o
X
o
X
X
o
X
X
X
X
o
X
X
X
X
X
X
X
X
X
X
X
X
X
o
X
o
o
o
X
X
X
X
X
X
X
X
o
X
o
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
o
X
X
o
X
o
X
X
X
X
X
o
o
X
o
X
X
X
X
X
X
X
X
o
o
X
o
X
o
o
X
o
X
X
X
X
o
o
X
X
o
o
X
o
o
X
o
X
X
21
20
14
12
17
26
11-2
Figure "-2. Spatial trend of major benthic taxonomic groups.
1983.
8
9,093
-
;::
, ,
, .
. ,
3.000
- Chironomidae
u--- Simuliidae
X
X
o
E
'- 2.500
o
z
; 2,000
u
c:
10
-g 1,500
:I
.Q
« 1,000
X
X
X
500
,
7
~. "'-~. .-. - _.)
I I
5 6
X
X
X
,
4
3
2
8
5.~40
X
X
o
o
X
600
- Trichoptera
-uno Ephemeroptera
--- Oligochaeta
450
"
II
/ \
/ \
/
I
_J
/
/
/
,
,
300
~ 250
o
z
;200
u
c:
~ 150
c:
:I
.Q
« 100
X
o
o
X
X
X
o
X
50
X
X
2
4 5
Stations
3
X
X
X
X
o
(mayflies) were present in low densities at Station 7.
but were most abundant at Station 8. Neither of these
two groups were abundant at the reference station
(Station 2). The dipterans (represented by simuliids
and chironomids) and oligochaetes were the principal
benthic components of the community in the de-
graded area downstream of the discharges. The
simuliids peaked at Stations 4 and 7 which were
located downstream of sewage treatment plants and
may have received nutrient enrichment from these
sources. All of these groups declined in abundance at
Station 8.
Two species each for the ephemeroptera (Caenis and
Baetis) and Trichoptera (Hydropsyche and Cheuma-
topsyche) reflected the abundance trends for those
groups (Table 11-2). The oligochaetes were not
identified any further than class level so key species
are not known for the 1983 survey. Cricotopus was
the numerically dominant midge in 1983. but Poly-
pedilum. Ablabesmyia, and Chironomus were also
abundant at certain stations.
X
X
o
X
X
o
o
X
o
31
-------
Table 11-2. Abundance (No./m2) of Benthic Macroinvertebrates Collected from the Ottawa River. July 1983
Station
Taxa 2 3 4 5 6 7 8
Coleoptera
Psephenus L. 7.57
Stenelmis L 248.60 11.30 158.20 3.73 11.30 67.80 387.93
Stenelmis A. 64.07 3.73 7.57 15.03 184.53
Dytiscidae 3.73
Agabetes L.
Dytiscus L. 3.73
Laccophilus A.
Hydrophilidae L. 3.73
Berosus L. 3.73 3.73 3.73
Berosus A. 3.73
Peltodytes A.
Total 320.24 15.03 158.20 3.73 30.06 86.56 583.65
Ephemeroptera
Baetis 3.73 169.50
Caenis 3.73
Stenonema 3.73 7.57 60.23
Total 3.73 3.73 11.30 229.73
Trichoptera
Cheumatopsyche 15.03 56.50 485.9
Hydropsyche 210.41 4,810.07
Hydropsychidae P. 22.60 210.97
Hydroptilidae L. 3.73 7.57
Hydroptilidae P. 11.30 26.33
Total 15.03 3.73 300.81 5,54084
Simuliidae
Simulium L. 101 .70 489.63 18.87 161.93 7,405.23 22.6
Simulium P. 45.20 192.1 7.57 18.87 1,687.43 7.57
Total 146.90 681.73 26.44 180.80 9,092.66 30.17
Chironomidae
Pupae 15.03 26.33 22.6 64.07 116.73 229.73 3.73
Procladius 3.73 3.73
Ablabesmyia 3.73 60.23 37.63 113.0 139.33 365.33 18.87
Chironomus 3.73 15.03 3.73 22.6 24103 158.2 7.57
C. (Dicrotendipes) 7.57 11.3 3.73 3.73
C. (Cryptochironomus) 7.57 18.87
C. (Tribelos) 22.6 7.57
Glyptotendipes 22.60 97.97 22.60
Polypedilum 7.57 12803 45.20 7.57 18.87 312.67 173.23
Stictochironomus 7.57
Tanytarsus 7.57 15.03 3.73 7.57
Zaurelia 7.57
Cricotopus 11.30 94.13 519.8 493.47 1,60833 1,348.43 56.5
Psectrocladius 3.73 7.57 7.57 11.3 22.6
Total 82.83 485.79 674.27 71 5.74 2,14689 2,433.12 290.07
Oligochaeta 52.77 131.87 143.17 5198 22.6
Miscellaneous
Hetaerina 3.73
Argia 11.3
Turbellaria 86.67 3.73
Hirudinea 757 3.73
Procambarus 30.17 3.73 1533
Hyallela azteca 18.87
Corixidae 3.73
Gastropoda (snail)
Ancylidae
Hemerodromia L. 56.5 30.17 3.73 11.30 3.73
Hemerodromia P. 11.30 7.57 22.60 15.03 18.87 3.73
Ceratopogonidae L.
Ceratopogonidae P. 3.73
Tabanidae L.
Chaoborus
Other 3.73
Total 128.14 82.83 52.77 18.76 7.57 7183 18.65
Total densities 599.01 734.28 1.702.57 907.84 2,88885 12,01888 6.693.11
Total no. taxa" 13 17 12 9 10 20 19
Community Loss Index 0.18 0.58 078 0.70 020 0.21
"Multiple life stages, higher taxonomic levels, and Oligochaeta are not Included in number of taxa.
Note: L. = larvae; A. = adults; P = pupae. 11-3
-------
11.3 Comparison Between 1982 and
1983 Surveys
The level of identification between the two surveys
was somewhat different so comparisons of composi-
tion and relative abundance are limited. The collection
techniques for quantitative assessment were similar
with the exception of the mesh size. The Hess
sampler used in the 1982 survey was equipped with a
363-pm mesh screen, and the Hess used in 1983 had
a 800-pm mesh screen. The larger mesh screen
would not capturt3the early instars or small organisms
encountered with the finer mesh.
Generally, the community composition of the benthos
was similar between 1982 and 1983. The numerically
dominant taxa during both surveys were simuliids,
chironomids. oligochaetes, and, to a lesser extent,
trichopterans and ephemeropterans. Spatial trends
of community parameters (number of species, total
abundance, community loss index) and major group
densities were similar between the two surveys
except for certain station shifts in peak densities.
Station 2 was the only reference area sampled in
1983 and did not produce a large number of species
or large abundances of sensitive species collected in
1982. Degradation of benthos was noted in both
surveys to occur downstream of the three primary
discharges with initial recovery occurring at Station
7. However, nutrient enrichment appeared to be
extensive at Station 7 in 1983 resulting in peak
densities of Simuliidae.
T T-4
-------
12.
Fish Community, 1983 Survey
All available habitats were sampled at each of the
seven biological stations using the same gear as in
1982. The proportional representation of each habitat
to the total sampling area at each station is not
available.
12.1 Community Structure
Twenty-three species of fish were collected in the
study area composing six families (Table 12-1). The
greatest abundance and number of species were
found at the reference station (Station 2). The redfin
shiner dominated the community at Stations 2
through 4, disappeared from Stations 5 and 6, and
then returned in small numbers at Stations 7 and 8.
The spotfin shiner became the numerically dominant
species of fish in the recovery community which was
found to occur at Stations 7 and 8. This species was
not found upstream of Station 7. Very few darters
were found in the study area. The darters were most
abundant at Station 2 but were also present at
Stations 3 and 8.
The Community Loss Index was the highest at
Stations 5 and 6, indicating that the greatest dis-
similarity in composition to the reference station
occurred at these two stations (Table 12-1 ). Stations
7 and 8 were most similar to Station 2 according to
the calculated index. The index indicated that the
communities at Stations 3 and 4 were marginally
affected by the discharges.
Fish abundance trends followed closely that of the
minnows with two species being particularly abun-
dant (Figure 12-1). The redfin shiner accounted for
over 80 percent of the fish at Stations 2 and 3.
Although the spotfin shiner was the numerically
dominant species of fish at Stations 7 and 8, it
represented <50 percent of the fish.
12.2 Comparison Between 1982 and
1983 Surveys
Compositional differences between the two surveys
were subtle and probably due to differences in the
level of effort and collection techniques. Abundances
were lower in 1983 and may also be attributed to level
of effort as well as natural seasonal fluctuation.
However, numerical dominance among the stations
was similar in both surveys with few exceptions.
Table 12-1. Results of Fish Collections in the Ottawa River,
July 1983
Station
Species 2 3 4 5 6 7 8 Total
G Izzard shad 4 2 6
White sucker 6 6
Golden shiner 4 4
Creek chub 15 4 4 56 80
Stoneroller 16 1 17
Fathead minnow 8 2 2 6 75 4 97
81untnose minnow 28 1 2 15 42 88
Spotf,n shiner 186 85 271
Emerald shiner 2 2 4
Redfln shiner 511 130 14 17 3 675
Sllverjaw minnow 7 7
Larval cypronlds 2 14 164 180
Rock bass 1 1
Largemouth bass 1 1
Green sunfIsh 2 4 6 2 14
81ueglll 6 17 2 25
Orangespotted sunfish 21 20 41
Pumpkinseed 1 5 7
WhIte crappie 36 36
Larval centrarchlds 2 12 38 17
Greenslde darter 5 1 6
Rainbow darter 1 1
Johnny darter 2 2
Black bullhead 1
Total organisms 628 142 22 27 9 396 363 1.587
Number 01 taxa 16 5 4 1 1 15 10 23
Community Loss Index 2.2 3.0 15.0 15.0 0.4 0.8
"Captured by dip net.
Minnows dominated both surveys, but the recovery
community in 1983 was dominated by spotfin shiners
compared to bluntnose minnows in 1982. Bluntnose
minnows were also. abundant in the recovery com-
munity at Station 8 (Table 12-1).
Results of the 1983 survey suggested a more
degraded fish community at Station 3 downstream of
the Lima Sewage Treatment plant (STP) discharge
than noted in 1982. However, one darter and the
second highest abundance of redfin shiners were
found at Station 3. The trend in recovery of the fish
community was similar to that indicated by the 1982
survey.
12-1
-------
Figure 12-1. Spatial trends of selected fish abundance.
July 1983.
628
-
400
350
300
250
200
150
100
50
511.
\
\
~
~
~
~
~
~
~
~
~
~
~
2
- Total Abundance
- - Redfin shiner
.--_... Spotfin shiner
'---
,"0.
,
,
I
---
3
4
5
6
7
8
Stations
72-2
-------
13.
Zooplankton Community, 1983 Survey
Micro- and macrozooplankton were only collected
during the 1983 survey using a Wisconsin stream net
with a 80-pm mesh net. These results are not
comparable to the drift results which emphasized
macrozooplankton and macroinvertebrate compo-
nents of the drift. Algae included in the plankton also
were identified and enumerated.
13.1 Community Structure
Total density of planktonic organisms fluctuated from
1 organism or cell per liter to a maximum of 35 per
liter (Table 13-1). The algal components of the
plankton were dominated by the dinoflagellate,
Ceratium. Rotifers, Brachionus in particular, were the
most abundant component of the zooplankton. Un-
identified cope pods and cladocerans composed the
crustaceans which were most abundant at Stations 6
and 7.
Generally, total plankton was least abundant at
Stations 3 through 5 (Figure 13-1). Algae constituted
nearly all of the plankton at Station 2 and represented
over 50 percent of the density at Stations 2 through 4.
Zooplankton increased from minimum levels at
Station 2 and peaked at Station 6. then decreased to
minimum levels at Station 8. Brachionus contributed
the single highest density at Station 6.
13.2 Evaluation of Zooplankton Com-
munity Response
Zooplankton abundance is relatively unimportant as a
stable trophic level in riverine systems and its
presence in low numbers at Stations 2 and 8 probably
represent normal population levels. The substantial
density increase observed at Station 6 may be due in
part to nutrient enrichment from some upstream
source, but is more likely attributed to a reduced level
of grazing because of an absence of predators at the
macroinvertebrate and plankton-feeding fish trophic
levels.
Table 13-1. Planktonic Organisms (number/liter) Collected from the Ottawa River, July 1983
Station
2 3 4 5 6 7 8
Crustaceans
Copepods 0.07 0.14 0.72 0.68 0.48 0.88 0.05
Nauplii 0.44 0.40 1.0 1.50 1.52 1.49 0.26
Cladocerans 0.14 0.08 0.42 5.15 2.52 0.20
Rotifers
Brachionus 0.07 2.48 6.7 21.92 9.6 0.05
Bdelloid rotifers 0.035 2.22 1.84 0.49 0.095
Keratella 0.27 0.13 0.28 0.16
Algae
Ceratium 33.39 10.36 6.16 1.5 0.12
Desmids 0.34 0.14 0.04 0.1 1.46 3.09 0.46
Pediastrum 0.34 0.61 0.56 0.22 0.03 0.12 0.05
Other
Chironomidae larvae 0.24 0.46 0.48 0.66
Nematoda 0.40
Total density 35.02 14.07 13.8 12.23 31.14 18.48 1.07
Total crustaceans 0.65 0.54 1.8 2.6 7.15 4.89 0.51
Total rotifers 0.30 2.42 4.6 7.35 22.02 9.6 0.05
Total algae 34.07 11.11 6.76 1.82 1.49 3.33 0.51
73-7
-------
Figure 13-1. Spatial trends 01 zooplankton components 01 the
plankton. July 1983.
40 - Total Plankton Density
-- Total Crustaceans
--u. -- Total Rotifers
'-
c:i
~
~
"iij
c::
~ 20
CI>
CI
."
~
>
oc(
30
10
,
,
,
-'
/"--.... "
""" ...
/ '" ...
~ '\\
.#/~
---
~ -----
2
6
3
4
5
Stations
13-2
.
.
.
.
.
.
\
,
,
7
8
-------
14.
Comparison of Laboratory Toxicity Data and
Receiving Water Biological Impact
A primary objective of the Complex Effluent Toxicity
Testing Program is to determine how effectively
effluent toxicity testing predicts impact to the biota of
the receiving system. The predictive capability of
toxicity tests can be assessed by comparing effluent
toxicity measurements (expressed as concentration-
based effect levels) to actual instream biological
impact (measured by standard biosurvey techniques).
Dye studies determine plume configurations over the
course of several days at a low flow period. Effluent
toxicity concentrations are then compared to effluent
concentration isopleths instream and biological im-
pact lones. Where effect level concentrations are
exceeded instream, biological impact is predicted. In
this study, a direct correlation between measured
effluent toxicity levels, instream concentrations, and
adverse impact to the biota in the receiving water was
considered a strong indication that measured effluent
toxicity does measure instream degradation and can
be translated directly into an assessment of adverse
water quality impact.
In the development of permit limits, a quantifiable
rela!ionship must be established between an effluent
and adverse impact to the local biota. Biosurveys are
useful in identifying impact but are of lesser value in
determining the amount of treatment needed to
reduce that impact. Further, where several dis-
chargers release wastewaters, impact assessment
using biosurveys can become complicated and diffi-
cult to interpret.
Toxicity data, expressed as an effect concentration
(such as a No Observable Effect Level or NOEL) can
provide the quantification needed to set treatment
requirements to reduce toxic water quality impact. If
the NOEL is not exceeded instream, it can be
concluded that no toxic impact will occur, assuming
that bioaccumulation/human health is handled else-
where and assuming that the proper NOEL is used.
A major difficulty in translating effluent toxicity to
instream impact is the practical limitations the
regulatory process places on data acquisition. Uncer-
tainty in comparing laboratory toxicity data to in-
stream impact arises when a limited amount of data
are available on the toxicity of the effluent and the
behavior of that effluent after discharge to the
receiving water. Scientific certainty in the translation
process is highest where a complete database is
available for a discharge situation. A complete data-
base would include acute and chronic toxicity data on
a wide spectrum of indigenous species, ecosystem
structure and function data, and daily exposure
analysis over a long period of time. Unfortunately,
ideal databases will be, practically speaking, non-
existent due to cost and analytical capability limita-
tions.
Two principle sources of uncertainty in the translation
process are species sensitivity and fate/persistency
after discharge.
To be effective indicators of adverse impact. the
species tested must be "sensitive" to the effluent's
toxicity. If the test organisms were not representative
of sensitive indigenous species in the ecosystem, the
effluent could exert a toxic effect on some of the
receiving water biota but not on the test organisms. A
false negative analysis would result.
Different species exhibit different sensitivities to
toxicants. There often are two orders of magnitude
difference between the least sensitive and the most
sensitive organisms when they are exposed to a
particular toxicant or effluent. This range varies
greatly and can be narrow or wide depending on the
toxicant or effluent involved. The primary goal in
toxicity analysis is to use a "sensitive" organism to
test effluent toxicity. A majority of the biota exposed
to that effluent in the receiving water will exhibit a
lower sensitivity to that effluent and will be protected
so long as that test organism's measured no-effect
level is not exceeded. Since the measured toxicity of
an effluent will be caused by unknown toxic consti-
tuents, the relative sensitivities of the test organisms
will also be unknown. Therefore, proper effluent
toxicity analysis requires an assessment of a "range"
of sensitivities of test organisms to that effluent. The
only way to assess sensitivity range is to test a
number of different species.
In this study, two organisms were used to assess a
range of sensitivity to the effluent toxicities of the
three dischargers. They exhibited different responses
to the different effluents. The test organism exhibiting
sensitivity at the lowest concentration for that effl uent
74-7
-------
was considered representative of the sensitive orga-
nisms in the receiving water.
Effl uent toxicity fate/persistence must be considered
in making the translation between laboratory toxicity
tests and adverse impact. As soon as an effluent
mixes with receiving water, its properties begin to
change. The rate of change of toxicity is a measure of
the persistence. In most cases, the level of toxicity
instream will drop as decay processes (photodecom-
position, microbial degradation) or compartmental-
ization processes (sediment deposition, volatilization)
occur and bioavailability decreases.
If the toxicity measured in laboratory toxicity tests is
quickly reduced or eliminated after discharge, the
translation between toxicity and impact will not be
valid.
Onsite toxicity testing from this study and other
subsequent studies has indicated that the toxicants
causing toxicity measured at discharge sites tend to
be persistent. There is little "near field" degradation
of the measured effluent toxicity. Effluent toxicity
does exhibit "far field" decay. Typical patterns of
progressive downstream decreasing toxicity (similar
to BOD decay) have been observed in a number of
discharge situations. In this study, ambient toxicity
test data were used to assess the fate/persistency of
measured effluent toxicity.
With these two sources of uncertainty taken into
consideration, the analysis of the effectiveness of
effluent toxicity tests to measure actual instream
impact was conducted.
14.1 Results of Integration Analyses
Regression analyses were performed using the
results of ambient toxicity tests and aquatic commun-
ity measures. The analyses indicate there is a
correiation between ambient chronic toxicity and the
number of species, community loss, and diversity of
the aquatic invertebrates and algae (Table 14-1). A
positive relationship existed between young produc-
tion of Ceriodaphnia and number of benthic species
(R=0.71) and benthic diversity (R=0.79), while a
negative correlation (R=0.63) was observed between
young production and benthic community loss (Figure
14-1). The good correlation between you ng produc-
tion of Ceriodaphnia and benthic parameters was a
result of an agreement in effects from the STP. The
number of benthic species decreased from 52 at the
reference station to 32 at Station 3, and a similar
reduction in diversity (from 3.6 to 1.7) occurred
between the reference station and Station 3 (see
Chapter 8). Young production for Ceriodaphnia did
not occur in tests on water collected from this station
(see Chapter 4) where the effluent from the STP
constituted over 50 percent of the flow (Table 6-2).
14-2
Table 14-1.
Comparison of Toxicity and Biological Response
Ambient Toxicity Biological Community
Impairment (%) Impairment (%)
1982 Data
o
100
52
63
19
o
o
1983 Data
o
91
59
71
86
77
5
Station
2
3
4
5
6
7
8
o
40
60
80
100
40
16
2
3
4
5
6
7
8
o
70
75
80
94
7
40
These data from the benthic survey and the Cerio-
daphnia testing indicate a severe chronic condition
below the STP which was attributable to that effluent.
The algal community also decreased in diversity
below the STP (see Chapter 7) which resulted in a
high correlation with young production of Cerio-
daphnia (Figure 14-2). The algal community appeared
to improve following the refinery discharge. However,
this apparent amelioration of effects was temporary
and was attributable to an influx of algae from the
refinery waste treatment pond.
No correlation resulted between Ceriodaphnia fecun-
dity and fish species and diversity. Effects on the fish
community between the STP and refinery were slight
(see Chapter 9).
Results of the effluent toxicity testing on larval
fathead minnows indicated that the STP did not
exhibit chronic toxicity to the fathead minnows. The
differences in response exhibited by the chronic
effects upon the fecundity of Ceriodaphnia and the
growth of larval fathead minnows indicate the need to
include measurements of chronjc toxicity of the
effluents for as many species as possible.
The effluent toxicities measured by the effluent
toxicity tests exhibited a high level of persistence.
This property can be verified by the analysis of the
ambient toxicity data. The ambient chronic toxicity in
the Ottawa River was reflected in the observed
impact from the field studies (Figures 14-3 and 14-4).
Chronic toxicity was measured at Stations 3, 4,5, and
6 (a distance of 14.5 km). It was at these stations that
the invertebrates, fish, and algae were impacted most
heavily. For the invertebrates and algae, the relation-
ship (as shown in Figures 14-1 and 14-2), is linear. At
Station 7, no chronic toxicity was observed in
Ceriodaphnia toxicity tests. This was the first station
where the benthos and algae began to show recovery.
-------
Figure 14-1. Correlation of Ceriodaphnia young per female
with benthic parameters from eight stations in
the Ottawa River. Lima. Ohio. 1982.
5
4
iii
0
.t:.
E
CD 3
a
~
'jjj
1u
> 2
o
i 1.5
.t:.
E
!
II)
II)
..9 1.0
~
'c
:I
E
E
o
u 0.5
(a)
.
R = 0.71
10
20
30
Young/Female
(b)
.
R = 0.79
-10
o
10
20
30
Young/Female
20
(C)I
.
.
.
R = 0.63
-10
o
10
Young/Female
20
30
Figure 14-2. Correlation of Ceriodaphnia young per female and
algal diversity at eight stations in the Ottawa
River. Lima. Ohio. 1982.
~ 3
co
~
~
co
1u 2
c:
CD
CJ
~
'jjj
1u 1
>
o
5
4
o
-1
-10
o
.
.
.
R = 0,79
10
Young/Female
20
30
Figure 14-3. Ambient toxicity correlation between
Ceriodaphnia young per female and"cological
survey data for 1982.
0;
...
'E
CD
.t:.
U
II) 50
CD
'u
~40
IJ)
II)
o
E 30
CD
lEI
'0 20
1u
.&J
~ 10
z
gJ 24
'u
~ 20
IJ)
~ 16
iL:
'0 12
~
~ 8
:I
Z 4
~--,,,,,
",
-----, "II"
\ ...-
\ '
\ 1
\ 1
\ 1
\ 1
\ I
\ "...,'
\ , '.... ,
\ , ....",
\ 1
\ 1
\ /
\ 1
2
3
70
iii 60
0
.t:.
E
CD 50
a
II)
CD
'u 40
CD
Q
IJ)
'0 30
~
..0
E 20
:I
Z
10
-10 0
4 5
Stations
6
7
25 ~
...
Q'
20 ~
~
::!-
;)
15 iii'
<-
o
c:
10 c5
"
CD'
3
15 I»
~
I
8
0;
,~
E
Il. CD
\ f 6J ",,,'''------
\ 1
\ '
\ '
\ '
\ /
\ '''''''''...'
\ """'...'
\ '
\ 1
\ /
\ 1
\, '
- ---Ceriodaphnia' I"')
- Fish species 24 ~
Q'
20 ~
~
16 5
iii'
12 ~
c:
8 c5
"
CD'
4 3
III
~
2
3
4 5
Stations
6
7
14-3
8
-------
Figure 14-4. Ambient toxicity correlation between
C"riodaphnia young per female and
ecological survey data for 1983.
" --- Ceriodaphnia
" \ > iii -'Benthos taxa
" \ ... u
, I ~ 'E
" , 11.. ;;: CD
, 'I- Q) .J::.
\(/) a:: u
\~\ I I
60
I 30
,
,
,
,
,
,
,
,
,
,
25 :;?
..,
Q'
c:a.
20~
~
::!
j;'
15 <"
o
c:
~
10~
iD'
3
5 !!!.
.!!.
50
IU
)(
IU
I-
...40
o
.J::.
E
~,30
'0
,8120
E
:I
Z 10
,
,
,
,
,
,
I
,
I
,
" "
... ,
... ,
'",,,'
2
3
8
4
6
1
5
Stations
32
...
,~ 28
GI
~24
.J::.
i!: 20
'0
.. 16
.8
E 12
:I
z
IU
,2
E
GI
.J::.
r
---.Ceriodaphnia 32
-Fish species 28 ~
, CD
: 245'
: I}
: 20 -g.
: ~
/ 16 ~
, <
o
12 5
CD
......
8 iD'
3
QJ
4~
>
..
GI
c:
~
GI
a::
I
"
/,
, ,
" ,
, ,C1.
,I-
'(/)
\~
,
,
,
,
,
,
,
,
,
,
,
,
,
, "'...
" .......,
, ...
, ...
, ...
, ...
, ...
, ...
, ...
" .....
8
4
2
3
4 5
Stations
8
6
7
The fish community did not recover fully until Station
9. The cause of delay in recovery is unknown, but
could have resulted from low dissolved oxygen or
other sources of pollutants, such as landfilileachates.
The difference in the sensitivity of Cer;odaphn;a and
fish could be the reason for the degradation of the fish
community between Stations 7 and 9 was not
predicted by Cer;odaphn;a toxicity. The relationship
between the fathead minnow test results and the fish
survey needs to be strengthened with further tests
using fathead minnows in ambient tests. However,
the effluent dilution tests with fathead minnows
agree well with the impact on the fish community.
14.2 1982-1983 Comparison
In 1982 the benthic population was most severely
impacted in the zone where the Cer;odaphn;a toxicity
was observed. At stations where there was up to a 50
percent reduction in Cer;odaphn;a fecundity, 50
percent of the macroinvertebrate species were lost
(Table 14-1, Figures 14-1, 14-3). Likewise, when less
chronic toxicity was measured, as indicated by the
14-4
production of young Cer;odaphn;a, the benthic diver-
sity increased. At Station 8 where the periphyton and
benthos had fully recovered, there was no ambient
toxicity measured. In 1983, the toxicity and impact
patterns of the Ottawa River from Stations 2 through
8 were quite similar. The number of benthic taxa
identified in 1983 (Figure 14-4) is not as large as in
1982 (Figure 14-3) because all the taxonomy was not
completed in 1983 (see Section 11.3). The maximum
toxicity was noted between Stations 3 and 6 and the
maximum biological community impairment occurred
at Station 5 in both years.
The fish community from Stations 2 through 8
responded similarly in 1982 and 1983. Subtle
differences in the spatial trends ofthe fish community
between 1982 and 1983 are probably due to differ-
ences in level of effort and collection techniques
between the two years (see Section 12.2). It should be
noted that a different group of chemicals were identi-
fied in the 1983 STP effluent from that present in the
1982 study. However, general effects at Station 3
were similar between the two years for both the fish
and invertebrates. Maximum impairment took place
at Station 6 where only one species was collected. In
1982 no fish were collected at this station; the
problem at Station 6 is unclear, although it was
suggested from the 1982 ecological survey (Chapter
9) that a delayed effect from high BOD may be
responsible. The number of benthic species (taxa)
increased at Station 6 from the immediate upstream
stations in both years. In 1983, however, the toxicity
impairment at Station 6 was nearly as great as
downstream from the STP This would indicate the
possible presence of additional toxicants. Subsequent
investigation indicates that there is an industrial
landfill adjacent to the river and seepage to the
Ottawa River may be taking place.
The relationship between Cer;odaphn;a toxicity re-
sponse and biological impairment is quite good during
each year. When such correlations exist as demon-
strated with the 1982 data, the reduction in toxicity
could be predicted to achieve a certain degree of
recovery. However, for some groups of organisms,
the pattern is not so clear. The lack of good correlation
could result from the displacement of ambient toxicity
caused by the variable nature of the effluent and
stream flow. In addition, members of the biological
community such as fish can move in response to a
gradient or be affected by other stresses such as
unfavorable dissolved oxygen or temperature levels.
Differences in toxicity response of laboratory test
animals and the variation of biological impairments
require that impacts in any community component be
considered important. In analyzing the toxicity test
data, toxicity to the greatest impairment indicated by
Cer;odaphn;a or fathead minnows, reproduction of
-------
Ceriodaphnia, or the growth of newly hatched fathead
minnows was used. Community impairment was
based on that portion of the community that lost the
highest percentage of species.
A method of comparing ambient stream toxicity and
biological community impairment was developed to
relate toxicity testing information to ambient com-
munity response (Table 14-1). The expected ambient
stream toxicity was calculated by determining the
minimum NOEL concentration ofthe effluent, regard-
less oftest species. The biological community impair-
ment was calculated by the maximum percent of
species lost (relative to a reference area) regardless of
trophic level. In 1982 downstream from the STP,
there was a 100 percent toxicity impairment and only
40 percent community impairment, whereas in 1983
there was a 91 percent toxicity impairment and a 70
percent community impairment. This yearly differ-
ence was due to the fact that in 1982, only the benthic
invertebrates and attached algae were impacted,
whereas in 1983 the fish community was severely
impacted. Downstream from the refinery at Station 4,
in 1982 there was 52 percent toxicity impairment and
a 60 percent biological community impairment (Table
14-1). In 1983, there was a 59 percent toxicity and a
75 percent community impairment. The similarity of
ambient toxicity and community impairment in this
reach indicates the ability to quantify chronic stream
effects.
The results downstream from the chemical plant are
the most difficult to interpret because of the upstream
toxicity. In 1982 the impact measured in the chemical
plant effluent by the toxicity test was from upstream
water. Likewise, the toxicity measured in the stream
and resultant biological impact probably resulted
from upstream sources. The ambient toxicity indicated
a E>3 percent reduction in reproduction, while the
measured biological impact was 80 percent. In 1983
the ambient toxicity measured caused an 88 percent
reduction in reproduction from upstream sources.
The biological community was reduced 80 percent.
Thus, the agreement between ambient toxicity and
community response is good.
In the recovery reach at Stations 7 through 8, the
agreement between predicted ambient toxicity impair-
ment and observed biological impairment is generally
quite good. However, because ofthe transitory nature
of the reach for both toxicity and measurement of
organisms, there are some stations where both
impairments are not equal. In the reach where full
recovery of the community is achieved, toxicity
impairment was not present.
In summary, there is a high correlation between
ambient stream toxicity and the number of species,
diversity, and community loss of aquatic inverte-
brates. The correlcition between Ceriodaphnia and
fish species at the same station was poor. Responses
of the algal community correlates well with the
Ceriodaphnia toxicity tests. Persistence of effluent
toxicity can be measured using ambient stream
toxicity. Use of more than one test species improves
prediction of biological impact. In addition, many
segments of the aquatic community are required in
the assessment of biological impact. Biological com-
munity impairment occurred to the same degree as
toxicity impairment. Where no toxicity was measured
from upstream effluents, some impairment ofthe fish
community was evident but none on the periphyton
and benthos. Both Ceriodaphnia and fathead minnow
chronic tests can be used to measure ambient toxicity.
These data appear to be directly relatable to biological
community impairment.
14.3 Calculation of Toxicity Reduction
Results of the effluent dilution tests analyzed together
with the calculated effluent concentrations in the
stream (determined by the dye dilution studies) allows
further comparisons to be made. The 7-day fathead
minnow chronic tests were conducted on the three
effl uents. The STP effluent at 100 percent concentra-
tion had no impact on growth of fathead minnows,
and the number of fish species (11) below the STP
outfall remained relatively high. Refinery waste of 50
percent caused nearly 90 percent mortality offathead
minnows in the effluent toxicity tests. The stream
below the refinery was approximately 30 percent
refinery waste. Only six fish species were found in
this area. The number of fish species continued to
decrease at the next three downstream stations
below the chemical plant. The effluent dilution tests
on the chemica I pia nt effl uent showed that the 100
percent effluent had no effect on fathead minnows.
There was high mortality in the controls and lower
concentrations of waste which contained upstream
dilution water contaminated with about 30 percent
refinery effluent. These concentrations were clearly
toxic and thus agreed with the expected toxic impact
which was observed in the reduced fish population in
the stream below the refinery.
The refinery effluent at 10 percent concentration
reduced fathead minnow survival 25 percent and at
50 percent concentration, growth was reduced about
60 percent. The Ottawa River downstream from the
refinery outfall is about 29 percent refinery wastes.
Using 10 percent refinery effluent as the no effect
concentration for fathead minnows and 29 percent as
the river concentrations of refinery effluent, a 2.9-
fold reduction in toxicity would be necessary. The
Ceriodaphnia young production was reduced 90
percent in all concentrations of the refinery effluent
as the result of the dilution water which contained
about 60 percent STP effluent. The no effect concen-
tration of STP effluent for Ceriodaphnia was between
14-5
-------
5 and 10 percent. If the concentration of 10 percent
STP effluent is used as the no effect concentration,
and considering that 77 percent of the Ottawa River
below the STP outfall is STP effluent. an approximate
7.7-fold reduction in toxicity would be required to
protect the community below the outfall at the flow
during the study. For both the STP and refinery
wastes, additional tests with smaller concentration
intervals would make the estimates of needed
reductions more precise.
The permissible loading must maintain a concentra-
tion less than or equal to the no effect concentration
at the critica I flow specified by the reg u latory agency.
For the Ottawa River, the permit limits are based on
the 7-day low flow in 10 years (7010). If one calcu-
lates the amount of toxicity reduction necessary to
remove chronic toxicity in the receiving stream at the
time of study, it must then be extrapolated to the flow
upon which the permit is based. The methods for
calculating the required abatement can be based on
ambient stream toxicity or effluent toxicity. There are
two approaches to calculating the required abate-
ment: the first is an engineering approach based on
Toxic Units (Toxic Unit Approach); the second is a
more biological approach which is based on stream
and effluent flow and the no effect concentration
(Concentration Approach).
The Toxic Unit Approach for calculating the required
abatement can be based on ambient stream toxic
units or effluent toxic units (TU). A toxic unit is the
inverse of an effluent concentration producing a
defined endpoint. e.g., if the no effect concentration is
10 percent, one would have 10 toxic units; for a 5
percent no effect concentration, 20 toxic units; for a
100 percent no effect concentration, one toxic unit.
The following data are used in the examples of
calculating abatement for the two approaches with
the STP and refinery data. Examples assuming
additivity of multiple effluents are also given.
Since the toxic units used here are based on cronic
toxicity, toxic units are designated as TUe.
Flows (m3/sec):
Flow
Flow Upstream
Upstream of
7010 of Chemical Chemical
of STP STP Refinery Refinery Plant Plant
0.071 0.36 0.43 0.20 0.62 0.055
No Effect and Effluent Toxic Units Data Toxic
No Effect Units
Discharger Concentration (TUcI
STP 10% 10
Refinery 3% 33.3
Chemical Plant 100% 1
For the following examples, assume that the river
upstream of the STP has 0.0 TUe.
14-6
Toxic Unit Approach
I. Sewage Treatment Plant Reduction
Calculation
A. Ambient Stream Toxicity Balance
Method:
For a single discharge, the equation is as follows:
Ambient = Effluent
TUc Flow
x Effluent + Upstream x
TUc TUc
Effluent + Stream
Flow Flow
Stream
Flow
(1 )
Thus using Equation 1, ambient TUe below the STP
can be calculated.
=0.36x 10+0.0xO.071
0.36 + 0.071
=8.35
[This is 7.35 TUc more (8.35-1 .0) than
permissible in the stream.]
In that the permissible stream TUe is 1.0, one can
calculate the reduction required as follows:
Reduction
Required (%)
=Ambient TUc - Permissible Stream TUc 100
Ambient TUc
=8.35 -1.0x 100
8.35
(2)
=88
B. Effluent Toxicity Calculation Method:
The required abatement to achieve a no effect level of
1.0 TUe in the stream is calculated:
1.0 = Permissible TUc x Effluent Flow
Stream Flow + Effluent Flow
(3)
1.0 = Permissible TUc x 0.36
0.071 + 0.36
Solving for permissible TUc,
Permissible TUc = 1.2 in STP effluent.
Required abatement based on TUe is,
Reduction
Required (%)
= Effluent TUc - Permissible TUc x 100
Effluent TUc
(4)
~ 10-1.2x 100
----;0-
=88
It should be noted that the reductions for the ambient
stream balance method and the STP effluent toxicity
method are the same (88%) because the upstream
TUe are assumed to be 0.0.
-------
II.
Refinery Reduction Calculation
I.
Sewage Treatment Plant Reduction
Calculation
A.
Ambient Stream Toxicity Balance
Method:
For this example, assume there is no additivity ofTUc
among discharges. That is, upstream of the refinery,
the ambient TUc is 0.0.
Ambient = 0.2 x 33.3 + 0.0 x 0.43
rUe 0.20 + 0.43
= 10.57
Reduction = 10.57 - 1.0 x 100
Required (%) 10.57
B.
= 91
Effluent Toxicity Method:
Again, the permissible TUc in the stream below the
refinery is 1.0.
1.0 = Permissible ru x 0.20
0.43 + 0.20
Permissible rUe = 3.2 in Refinery Effluent
Required abatement based on TUc is thus,
Reduction = 33.3 - 3.2 x 100
Required (%) 33.3
=90
Concentration Approach
This approach utilizes biological effects concentra-
tions such as the NOEL for calculating the reduction
required rather than the engineering terms of the
Toxics Unit Approach.
To avoid impairment in the stream, the instream
waste concentrations (IWC), which is the effluent
concentration in the stream after complete mixing,
must be equal to or less than the NOEL a as determined
in the effluent dilution test. Conversely, for a given
waste concentration in the stream, the NOEL must be
a percent waste that is equal to or greater than the
IWC. Further, for determination of treatment require-
ments, the IWC must be less than or equal to the
NOEL at the critical low flow as specified in the
applicable standards.
'Occasionally, tha NOEL is calculated as the geometric mean of the lowest
concentration that produces an effect and the highest concentration that
does not produca an effect; but for large concentration intervals as used
here, a better estimate is the lower of the two values.
For the Ottawa River the critical flow is specified as
the 7010. During the study period the flow was 0.071
m3/sec (-7010) above the STP outfall. Thus,
Iwe (%) = Effluent Flow x 100
Effluent + Stream Flow
(5)
(1 )
=
0.36 x100
0.36 + 0.071
=84
(2)
The NOEL was approximately 10 percent for the STP
effluent using the Ceriodaphnia test, so the required
reduction is:
Reduction = Iwe - NOEL x 100
Required (%) Iwe
(6)
= 84 - 1 0 x 1 00
84
=88
(3)
The lowest permissible NOELofthe waste must equal
the IWC which for the STP is 84%.
(4)
To determine the toxicity reduction needed for a
critical flow different from the ones used in the
example above, substitute that flow into equations 5
and 6 and solve. (For further explanation see
footnote a.)
II.
Refinery Reduction Calculation
The data gathered in the 1982 study do not permit any
similar calculations for the reduction required for the
refinery because the dilution water for the refinery
'One can show that Equation 6 can be derived using Equation 4 as follows:
Reduction Effluent TUe - Permissible TUe ~ 100 (4)
Required (%) Effluent TUe
Where,
!:ffluent TUe - ---1-
NOEL
Permissible TU
-1- (for ambient TUe set at 1.0)
Iwe
By substituting into Equation 4,
ReductIon
Required (%)
1 1
NOEL iWC x 100
1
NOEL
Then simplifying,
Reduction
Required (%)
Iwe - NOEL x 100
Iwe
14-7
-------
test was toxic due to the STP effluent contained in it.
In the 1983 study, the refinery effluent was diluted
with water not containing STP effluent. In that test,
the NOEL was between 10 and 3 percent concentra-
tions. Using 3 percent as the NOEL and the 1982 flow
of 0.43 m3/sec:
Iwe % = 0.20 x 100
0.29 + 0.43
= 32
Reduction = 32 - 3 x 100
Required (%) 32
= 91
The lowest permissible NOEL of the waste must equal
the Iwe which for the refinery is 32%.
This calculation assumes that the STP concentration
in the upstream water is at or below the NOEL and
that there is no additivity to the toxicity of the refinery
waste by the STP effluent present. If discharge limits
were to be developed, the best approach would likely
be to permit no more than the NOEL of each one. The
protectiveness of these concentrations could be
tested by adding a concentration of each effluent
equal to the NOEL to upstream water to see if jointly,
any impairment would occur. If it did, then a next step
would be to try dilutions of the mixture of the two
NOELS in order to determine where there is no
impairment. These then would become the permis-
sible Iwe for the critical flow.
In the examples above, the toxic effects of the wastes
have been assumed to be non-additive. From the
Ottawa River and other studies, wastes have been
found to be generally non-additive. On occasion
when the discharges were from the same type of
industry (Le., metal finishing), the toxic effects were
additive. In no study was synergism found. In some
studies one effluent rendered another effluent less
toxic even though they were both toxic before mixing.
Multiple Effluents - Additivity
For multiple effluents that are believed to be additive,
and when allocation is necessary, then the policies of
the regulating agencies should be followed. There are
many possible allocation approaches: (1) upstream
design flow, (2) equal degree of treatment, (3) equal
loading, (4) equal reduction. There could be other
bases for allocation, all of which are based on policy
rather than science. The approach used for dissolved
oxygen waste load allocation could be applied most
directly. Examples of the biological and engineering
approaches are presented to illustrate the simplicity
of calculation.
14-8
Toxic Unit Approach-Additivity
The ambient TUe as calculated for two or more
effluents is as follows:
(5)
Ambient =
rUe
n m
I (Effluent x Effluent) + I (Additive + Stream)
i=1 Flow; rUe; j=1 Stream Fiowl rUel
n m
I Effluent + I Additive
i=1 Flow; j=1 Stream Flow
(4)
(6)
Where, n = number of effluents
m = number of upstream and tributary flows
And, additive stream flow includes upstream, up-
stream effluent and tributary flows.
The above equation can be used siry1ilarly to Equation
,. to calculate the ambient TUe and the permissible
TUe. To solve for permissible TUe. one must start with
the upstream discharge and work downstream.
The equation for the STP would be the same as before
since it is the most upstream discharge.
To calculate permissible TUe in the downstream
effluents such as for the refinery, the above equation
can be simplified because the ambient TUe below the
STP (which is above the refinery) is set at 1.0 and
likewise the ambient TUe downstream of the refinery
is set at 1.0.
The permissible TUe for refinery is calculated:
1 .0 = 0.20 x Permissible rUe + 0.431 x 1 .0
0.20 + 0.431
(7)
Permissible rUe = 1.0 in Refinery Effluent
Reduction = 33.3 - 1.0 x 100
Required (%) 33.3
(4)
= 97
In the above allocation procedure the benefits of
having no toxic units in the upstream flow is only
realized by the STP and not by the refinery.
If the allocation of the upstream flow is shared equally
(0.071/2 = 0.0355) the required abatement is cal-
culated:
For the STP:
1.0 = 0.36 x Permissible rUe
0.36 + 0.0355
(7)
Permissible rUe = 1.1 in srp Effluent
Reduction
Required (%)
1LL.1 x 100
10
(3)
=89
-------
And, for the refinery:
1.0 = 0.36 x 1.1 + 0.20 x Permissible TUe + 0.0355 x 0.0
0.20 + 0.431 (7)
Permissible TUe = 1/18 in Refinery Effluent
(which compares to 1.0 when dilution was
not equally shared)
Reduction
Required (%)
33.3 - 1.18 x 100
33.3
= 96
The differences for this additivity example are small
because of the small amount of dilution flow com-
pared to effluent flow.
Concentration Approach-Additivity
When additivity is assumed using the Concentration
Approach, the NOEL should be reduced for each one.
If this is done by lowering each one equally the
calculation would then be for the STP:
NOEL = ~
2
=5
Reduction
Required (%)
84-5x100
84
= 94
Permissible = ~
Toxicity (%) 2
=42
And, for the refinery:
NOEL = ~
2
1.5
Reduction
Required (%)
= 32 - 1.5 x 100
32
= 95
Permissible
Toxicity (%)
R.
2
=16
These values for the STP and the refinery, 94 and 95
percent, respectively, compare to 88 and 91 percent
under the no additivity assumption. Obviously, other
scenarios can be done comparably. The STP could be
given two-thirds of the dilutibn capacity and the
refinery one-third. All that is needed to calculate the
(3)
reduction required is to multiply the STP NOEL by
two-thirds and the refinery NOEL by one-third and
recalculate Equation 6 for each one. Reductions can
be calculated based on partial additivity. For example,
1.5 NOEL could be allowed below the refinery. If the
division of dilution is to be equally proportioned
between both dischargers, then 0.75 of each NOEL
would be substituted in Equation 6. Three or more
discharges are handled identically.
A slightly different case occurs if, for example, the
refinery decides to reduce toxicity by reducing effluent
flow. In this instance, Equation 5 must be solved for
the new expected flow before Equation 6 is solved. In
this example, the upstream discharge, being a STP,
would not likely be able to reduce flow, but where the
upstream discharge does reduce effluent flow, the
reduction required of downstream discharges will be
changed because tota"1 flow (effluent and stream flow)
will change according to Equation 5.
(6)
(6)
14-9
-------
References
American Public Health Association, American Water
Works Association, and Water Pollution Control
Federation. 1981. Standard Methods for the Exam-
ination of Water and Wastewater. 15th edition.
APHA, Washington. 1,134 pp.
Beck, W. M. 1977. Environmental Requirements and
Pollution Tolerance of Common Freshwater Chiron-
omidae. Environmental Monitoring Series EPA-
600/4-77-024. U.S. EPA, Cincinnati.
Davies, D. M., B. V. Peterson, and D. M. Wood. 1962.
The Blacktlies of Ontario, Part I. Adult identification
and distribution. Proc. Entomol. Soc. Onto 92:70-
154.
Engineering Science. 1981. Ottawa River Study.
Prepared for the Standard Oil Company (Ohio) in
association with TenEch Environmental Engineers,
Inc. 157 pp. plus appendixes.
Hamilton. M. A.. R. C. Russo. and R. V. Thurston.
1977. Trimmed Spearman-Karber Method for
estimating median lethal concentrations in toxicity
bioassays. Environ. Sci. Technol. (11 ):714-719.
Harris. T. L. and T. M. Lawrence. 1978. Environmental
Requirements and Pollution Tolerance of Trichop-
tera. Environmental Protection Agency Research
Report EPA-600/4-78-063. U.S. EPA. Washington.
Hilsenhoff. W. L. 1981. Aquatic Insects of Wisconsin.
Wisconsin Geological and Natural History Survey.
60 pp.
Hubbard, M. D. and W. L. Peters. 1978. Environmental
Requirements and Pollution Tolerance of Ephemer-
optera. Environmental Protection Agency Research
Report EPA-600/4-78-061. U.S. EPA, Washington.
Martin, G. L.. T. J. Balduf. D. D. Mcintyre, and J. P.
Abrams. 1979. Water Quality Study of the Ottawa
River, Allen and Putnam Counties, Ohio. Prepared
for Ohio EPA. 35 pp.
Mount. D. I. and T. J. Norberg. 1984. A seven-day
life-cycle Cladoceran toxicity test. Environ. Toxicol.
Chem. 3(3).
Norberg, T. J. and D. I. Mount. In Press. A new
subchronic fathead minnow (Pimephales promelas)
toxicity test. Environ. Toxicol. Chem.
Palmer. C. M. 1977. Algae and Water Pollution. U.S.
EPA Report No. 600/9-77-036. 123 pp.
Patrick, R., J. M. Bates, J. R. Gabel. M. H. Hohn, H.
Jacobs, S. S. Roback, S. Ruigh. and Y. Swabey.
1956. Biological and Chemical Studies for the Lima
Refinery, Standard Oil Company (Ohio). Acad. Nat.
Sci. of Philadelphia, Dept. of Limnology, Philadel-
phia. PA. 106 pp.
Spencer, D. R. 1978. The Oligochaeta of Cayuga Lake.
New York with a redescription of Potamothrix
bavaricus and P. bedoti. Trans. Amer. Micros. Soc.
97(2): 139-147.
Steele. R. G. D. and J. H. Torrie. 1980. Principles and
Procedures of Statistics. McGraw-Hili, New York.
481 pp.
Stone, A. 1964. Guide to the Insects of Connecticut:
Part IV. The Diptera or True Flies of Connecticut.
Ninth Fascicle. Simuliidae and Thaumaleidae.
State Geological and Natural History Survey of
Connecticut. Bulletin No. 97. Department of Agri-
culture and Natural Resources.
Trautman. M. B. 1957. The Fishes of Ohio. Ohio Univ.
Press, Columbus. OH. 683 pp.
U.S. Environmental Protection Agency. 1973. Bio-
logical Field and Laboratory Methods for Measuring
the Quality of Surface Waters and Effluents. U.S.
EPA Report No. 670/4-73-001.
Weber, C. I. 1973. Recent developments in the
measurement of the response of plankton and
periphyton to changes in their environment. in
BioassayTechniques and Environmental Chemistry
(G. E. Glass, ed.). pp. 119-138. Ann Arbor Sci. Publ.,
Ann Arbor, MI.
R-t
-------
Appendix A.
Toxicity Test Methods
A.1
1982 Methods
For the effluent dilution (ED) tests. a grab sample of
stream water was collected from just upstream of
each outfall in the afternoon of the day before it was
used. The effluent was collected as a 24-hour
composite sample by continuously pumping approxi-
mately 10 ml/min from the discharge flow. Each daily
composite was begun around 0800-0900 hours. All
discharges were relatively constant. so the composite
was essentially flow-proportional.
Dilution water was warmed to room temperature
overnight and effluent samples were warmed on a
hot plate to room temperature when test solutions
were made for the ED tests. Samples for the ambient
test were warmed as soon as they were brought to the
lab and the animals transferred on the day of sample
collection.
The various concentrations were made by measuring
effluent and stream water using graduated cylinders
of various sizes and mixing each concentration in a
3.8-liter polyethylene jar. Enough was mixed at one
time for both the fathead minnow and Ceriodaphnia
test. All samples were at or near dissolved oxygen
(DO) saturation when solutions were made up except
for Stations 4A through 7 of the ambient test. No
chemical measurements for specific chemicals were
made. Routine water chemistry such as DO and pH
was measured in various samples daily, and many of
the DO measurements were made just before chang-
ing test solutions to determine the minimum values
occurring.
Test solutions were changed daily so that in the ED
tests, the fish and Ceriodaphnia were exposed to a
new 24-hour composite effluent sample each day.
The dilution water was a new daily grab sample of
receiving water. For the ambient tests, only Cerio-
daphnia were tested and they were placed in a new
daily grab sample each day. The controls for the STP.
refinery. and chemical plant ED tests were in the
same water as the animals in the ambient tests for
Stations 2, 3B, and 4, respectively.
For the fathead minnow larval growth tests. a
chamber 30 cm x 15 cm x 10 cm deep was made and
divided by three glass partitions which resulted in
four compartments 13 cm x 7.6 cm x 10 cm deep. The
partitions stopped 2.5 cm short of one side of the
chamber and a piece of stainless steel screen was
glued from one chamber end to the other and across
the ends of each compartment. This left a narrow
sump 2.5 cm x 30 cm x 10 cm deep along one side of
the chamber to which each of the four compartments
was connected by its screen end (Figure A-1). In this
way. the compartments could be filled and drained by
adding to or removing water from the sump. while the
fish in the compartments remained relatively undis-
turbed. This design a lIowed four "replicates" for each
concentration. These were not replicates in the pure
statistical sense because there was a water connec-
tion between compartments. However, there was
virtually no water movement between compartments
except when the compartments were filled or drained.
Each day. 0.1 ml of newly hatched brine shrimp was
fed three times and survival was counted. Live brine
shrimp were available during the entire daylight
period of 16 hours. Light intensity was very dim. The
compartments were siphoned daily usi'ng a rubber
"foot" on a glass tube to remove uneaten brine
shrimp. Additional test solution was removed from
the sump until about 500 ml remained in the four
compartments combined. leaving a water depth of
about 1 cm. Then, approximately 2.000 ml of new
test solution was added slowly into the sump. The
larval fish were able to maintain their position against
the current easily while the chambers were filled.
Fish were assigned to compartments one or two at a
time in sequential order. They were less than 24
hours hatched at the test beginning and were
obtained from the Newtown Fish Toxicology Labora-
tory culture unit. At the end of the test, the fish were
rinsed in distilled water. oven-dried at 98°C for 18
hours, and .weighed on an analytical balance. Four
lots of 10 fish were preserved at the beginning of the
test and later weighed to estimate initial weight. The
method is further described in Norberg and Mount (in
press).
The Ceriodaphnia from the Environmental Research
Laboratory-Duluth (ERL-D) culture unit. were placed
one animal to each of ten 30-ml beakers for each
concentration or sample tested. Each beaker coo-
tained 15 ml of test water; a newly born Ceriodaphnia.
less than 6 hours old, was added. One drop of a yeast
A-I
-------
Figure A-1.Test chamber for static renewal fathead minnow larvae growth test.
I
I
I --
-
, -1.:
,.,' -- --....
. -
;.. .,...
"-
.....
-
-
k--
- -
-
-
-
-
-
-
-
-
food, containing 250 /JQ, was fed daily. Each day, the
animal was moved to a new 15-ml volume with an
eye dropper, and the yeast food again was added.
When young were present, they were counted and
discarded. Temperatures were maintained at 23-
25°C. For the ED tests, the same concentration and
change schedules were used as described for the
fathead minnows. Mount and Norberg (1984)describe
the culture procedures and test method with Cerio-
daphnia.
Light was kept very dim to avoid algal growth and to
keep conditions comparable to those used for cul-
turing at Duluth. The high bacterial content of the
water and waste samples increased available food
and, where toxicity was not present, better young
production was obtained than where the only food
was the yeast, as was the case for the refinery test
using Lake Superior water for dilution.
The median lethal concentrations (LC50s) were
determined using the trimmed Spearman-Karber
procedure (Hamilton et al. 1977). Significant differ-
ences among the LC50s were determined by one-way
analysis of variance and Duncan's multiple range
test.
A-2
-
...-
k----
- -
-
-
--
--
--
--
-
--
-
--
-
-
--
-
-
-
-
A.2 1983 Methods
In 1983, one 19-1iter grab sample was collected for
each ambient station; 24-hour composite samples of
each effluent were collected. The samples were
cooled to 8°C and transported back to ERL-D where
effluent dilution tests and ambient tests were run
with both Ceriodaphnia and the fathead minnow. The
fathead minnows were less than 24 hours hatched
and were obtained from the ERL-D culture unit. Test
and analyses procedures followed the description in
Part 1. Temperature was maintained at 25::t1°C
during these tests.
-------
Appendix B.
Hydrological Field and Analytical Procedures
Dye was injected continuously for approximately 24
hours at each site to establish an equilibrium
between the injection-point dye concentration and
the downstream dye distribution. On the second day
of each study, water samples were collected at 12
transects extending from 30 m above to 1,520 m
below the point of discharge. The transect locations
with respect to the three discharges are illustrated in
Table 6-1. The ratio of the dye concentration at the
point of discharge to the dye concentration in the
water samples collected at the downstream transects
represents the dilution undergone by the effluent.
Rhodamine WT dye was injected at each site by a
Fluid Metering, Inc. precision metering pump. The
injection system was placed at a sufficient distance
from the river to allow complete mixing of the dye and
effluent prior to the point of discharge. The weight of
the dye container was periodically recorded to
monitor the dye injection rate. The Rhodamine WT
dye used in the study decays in the presence of
chlorine. Sodium thiosulfate, Na2S203, reduces the
chlorine to chloride when present in a concentration
approximately six times as great as the chlorine level.
At. the Lima STP a second Fluid Metering, Inc.
precision metering pump injected a 400 gm/liter
solution of Na2S203.
A flow-through Turner Designs fluorometer was set
up where the discharge from each site enters the
river to provide a continuous record of discharge dye
concentration. The fluorometer reading was recorded
on a Rustrak strip chart recorder. The temperature at
the discharge was recorded using a YSI probe and an
Esterline Angus strip chart recorder because the
fluorometer reading is temperature-dependent. Prior
to the field survey, the two fluorometers used had
been calibrated over a range of 0-124 ppb dye.
During the ambient survey on the second day of dye
injection, water samples were collected in 200-ml
bottles. A sample was taken and the water depth
recorded every 3 m across the transect, except near a
discharge or at a narrow transect where a 1.5-m
interval was used for greater resolution. A manual
sampler was set to take the water samples 0.2 m from
the bottom. When the depth was less than 0.25 m, the
sample was taken at middepth. If the water depth was
greater than 0.5 m, a second sample was taken 0.1 m
from the surface. Water samples were processed on
the same day of the instream survey using a Turner
Designs fluorometer in the discrete sample mode.
The fluorometer calibration was checked with field
standards each day it was used. As part of each
ambient survey, a flow measurement was taken at a
transect located 152 m upstream of the STP using a
Teledyne Gurley Pygmy flowmeter. This upstream
flow, coupled with the reported discharge flows,
allowed the river flow to be calculated below each
discharge.
The fluorometer data was converted to dye concen-
tration, C(ppb), using the relationship
C(ppb) = SR exp(0.027(T-20))
where
S = slope from the calibration
regression for the appropriate
sensitivity scale of the
fluorometer
R = fluorometer reading
T = temperature of the grab
sample at the time it was
processed
exp(0.027(T -20)) = correction factor for the
temperature dependence of
fluorescence (20°C is the
reference temperature)
In a similar fashion. the fluorometer readings from
the discharge strip chart recorder were reduced every
30 minutes for the duration of the study. The
background levels (equivalent dye concentration
fluorescence) measured upstream of the discharge
and in the effluent prior to dye injection were flow-
weighted to determine a background level which was
subtracted from the ambient data.
The 48-hour interval between collecting a set of
water samples at each site was considered sufficient
for the dye from the previous 24-hour injection to
flush out of the current 1.500-m study area.
8-'
-------
On 20 and 21 September, a dye integrity study was
performed by adding Rhodamine WT dye to an
effluent sample from each of the three sites. For each
site a 50 ppb dye solution was made in order to
represent the dye-injection concentration, and a 5
ppb dye sol ution was made by di I uti ng a portion of the
50 ppb solution with upstream river water. The
solution for the STP also contained sodium thio-
sulfate. Each solution was measured in the fluoro-
meter immediately after mixing, one hour later, and
one day later. No noticeable decay was observed in
any of the samples.
8-2
-------
Appendix C.
Biological Methods
C.1 Periphytic Community
Natural substrates (rocks) were sampled quantita-
tively using an epilithic algal bar-clamp sampler at
each of nine stations. All samples were taken from
the lower end of riffle areas and runs located at each
station. Four replicate samples were taken at each
station for chlorophyll a and biomass measurements.
These samples were filtered using 0.4S-Jlm filters
and stored in ice to await analysis in the laboratory.
One sample consisting of a composite of two bar-
clamp collections was taken from each station for
cursory identification (genus level) and abundance
estimates. These samples were preserved in M3
preservative to await analysis.
Ash-free dry weights (AFDW) and chlorophyll a were
analyzed from the filters in the laboratory. A small
plug (of equal size) was removed from each filter for
chlorophyll a analyses. The plugs of the filters were
macerated, and chlorophyll a was extracted with a
chlorophyll a standard (Sigma Chemicals) extracted
in a 90 percent acetone solution. Chlorophyll a
standing crop was expressed as milligrams per square
meter (mg/m2). For AFDW, the remaining portions of
the filters were dried at 1 OsoC to a constant weight
and ashed at SOooC. Distilled water then was added
to replace the water of hydration lost from clay and
other minerals. Samples were redried at 1 OsoC, and
biomass standing crop was expressed in grams per
square meter (g/m2). The biomass and chlorophyll a
data were used to calculate the Autotrophic Index
(Weber 1973), which indicates the relative proportion
of heterotrophic and autotrophic (photosynthetic)
components in the periphyton. The biomass and
chlorophyll a data were also statistically tested by
analysis of variance (Steele and Torrie 1980) and
multiple comparison tests to detect significant (P
~.OS) differences between sampling locations.
For identification and enumeration, each sample was
mixed for 30 seconds in a blender to disrupt algal
clumps, and the sample volume was then increased
to 2S0 ml. Ten percent of each thoroughly mixed
sample was removed to prepare Hyrax slides, which
were examined at 1,2S0X magnification to confirm
the identity of diatoms encountered during the
quantitative analyses. A 0.1-ml aliquot from each
quantitative sample was placed in a settling chamber
designed for use on an inverted microscope. The
chamber was then filled with deionized water, and
periphytic forms were allowed to settle to the bottom
of the chamber for 24 hours. Samples were examined
at 1 ,OOOX magnification with an inverted microscope,
and algae were identified to genus. For each example,
one diameter ofthe counting chamber was examined,
and algae containing protoplasm were enumerated
as cells except for genera of filamentous blue-green
algae, which were counted in 10-Jlm units of length.
The actual number of cells identified and counted in
each sample ranged from 126 to 2,S36, but was
greater than 400 in all but two samples. Periphyton
abundance was expressed as number of cells per
square millimeter (cells/mm2), and genus diversity
and equitability were calculated by USEPA methods
(EPA 1973).
C.2 Benthic Macroinvertebrate
Community
Benthic samples were collected from all nine stations
in 1982 with a Hess stream sampler (881 cm2). Five
replicate samples were collected from the riffle habi-
tat at each station. The mesh size on the Hess sampler
is 363 JIm, thereby retaining early instars of macro-
invertebrate life stages. Samples were preserved in
10 percent buffered formalin and returned to the
laboratory for analysis.
Water quality measurements consisting of tempera-
ture, dissolved oxygen, pH, and conductivity were
taken at every station. The water quality for the
biological field efforts are discussed in Section 4.1.
Drift collections were made at reference Station 2
and affected Stations 3, 4, and S. The stream drift nets
were 30.S cm x 4S.7 cm x 3.7 cm, made of SOO-Jlm
mesh nytex screen, and were anchored in the run
areas of each station. Four replicate samples were
collected from each station. Drift sampling was
conducted after dark, and nets were left in place for
30 minutes. Velocity measurements were taken in
front of each net with a Gurley Pygmy flow meter to
enable quantification of the data.
During the 1983 survey, three quantitative samples
were taken at the quarter points across the riffle at
each station using a standard Hess sampler (881 cm2
C-T
-------
with a 800 x 900-pm mesh screen). A qualitative
sample was taken by combining kick sampling from
recognized different habitats using a dip net with
500-pm mesh. Benthic samples were transferred in
total into glass jars and preserved in 10 percent
formalin.
The benthic samples contained large amounts of
detritus and organisms and were subsampled to
expedite organism sorting and identification. Sub-
sampling of the 1982 samples was done using EPA's
pneumatic rotational sample splitter (patent pending).
Samples were sorted with the aid of a Wild M-5
dissecting microscope. Organisms were sorted into
major taxonomic categories and preserved in 70
percent alcohol for later identification; organisms
were identified to the lowest practical taxon using
appropriate keys and. references. Oligochaetes and
chironomid larvae were mounted on microslides prior
to identification.
C.3 Fish Community
Fish collections during the 1982 survey were made in
92.3-m sections of stream at each of the nine Ottawa
River stations. Each sampling area contained pool
and riffle habitats, although in widely varying propor-
tions (Table C- 1). The riffle was upstream of the pool
at all stations except 5 and 6. The riffles were
considered natural barriers to the pool-dwelling fish
and a block net was placed at the opposite end of each
station to act as a barrier to escape.
Table C.,.
Station Pool, Riffle Proportions, and Number of
Seine Hauls
Pool Riffle
% of Number % of Number
Station Station Hauls Station Kick-semes
1 90 6 10 5
2 70 6 30 7
3 40 4 60 15
4 75 6 25 10
5" 40 5 60 18
6" 70 6 30 9
7 50 6 50 11
8 15 2 85 14
9 70 6 30 2
"Pool upstream of riffle.
The pools were sampled using either a 1 2-m or 13.8-
m x 3.7-m deep bag seine with 0.3-cm mesh. A 10.2-
m x 3. 7-m deep straight seine with 0.3-cm mesh was
used in the riffles employing the "kick seine"
technique. The number of seine hauls or kick seines
varied according to the width and other physical
characteristics to ensure complete sampling of the
area within the station.
Water temperature, dissolved oxygen, specific con-
ductance, and pH were measured during fish collec-
C-2
tions at each station. A Hydrolab Model 4041 was
used for all measurements.
During the 1983 survey, fish were collected using a
3.7-m x 27.7-m x 0.3-cm woven seine. Extensive
sampling was conducted in all recognizable habitats.
The small fish were killed in ice water and preserved
in 10 percent formalin. The few large fish were
identified in the field and released.
C.4 Fish Caging Study
The caging study was conducted using commercially
available plastic minnow traps with the openings
plugged with rubber stoppers. The maximum mesh
size was 4 x 8 mm. Total volume of each cage was 10
liters. Three cages were used at each of six stations,
and were labeled Rep A, B, and C, from downstream
to upstream. Each cage was secured to the bank with
a light line.
Fish used in the caging study were collected from two
upstream locations (Thayer Road and Cool Road). The
redfin shiner (Notropis umbratilis) was selected for its
abundance and relative ease of identification with
minimal handling stress. The fish were transported
and held in a large stainless steel tank containing
approximately 230 liters of water. At each station, 10
fish were transferred from the holding tank to the
minnow trap contained in a 1 9-liter bucket filled with
receiving water for transport to the caging site. To
reduce stress at each handling, care was taken to
move the fish quickly but gently in either a very fine
mesh net or a small quantity of water cupped in the
hand.
Observations were made daily at approximately the
same time and the number of live fish recorded. Dead
fish were removed and discarded. At the end of six
days, all remaining live fish were removed and frozen
for bioaccumulation analysis to be performed by EPA
labs in Duluth.
C.5 Zooplankton
A Wisconsin stream plankton net with 80-pm mesh
screen was used to collect zooplankton from each
biological station in 1983. Water velocities were
determined by timing the drift of a float (small leaf)
over a 9.2-m measured distance. The net was exposed
in this course for a duration of 2 minutes. Two
replicate samples were collected consecutively at
each station. Each sample was preserved with 10
percent formalin and stored in a 1 20-ml glass jar.
In the laboratory, the volume of each replicate sample
was determined to the nearest ml with a 250-ml
graduated cylinder. After mixing, 1 ml was transferred
to Sedgewick-Rafter counting chamber and the total
subsample strip scanned at 40X using a compound
microscope. Two such subsamples were analyzed
from each replicate sample.
-------
Appendix 0
Support Biological Data
rlble D-1. Abundlnce (ceUs/mm2) of Periphytic Algae on Natural Substrates in the Ottawa River, September 1982
Sampling Stations
2 3 4 5 6 7 8 9
BACILLARIOPHYTA (Diatoms)
Centrales
Cyclotella 3,392 9.279 499 1.596 100 1.895 200 399 499
Melosira 0 0 0 0 0 0 0 200 0
Skeletonema 0 1.895 299 698 100 0 0 0 399
Stephanodiscus 0 299 0 299 0 499 0 0 100
Thalassiosira 0 499 0 0 0 0 0 599 100
Total Centrales 3.392 11.972 798 2.593 200 2.394 200 1.198 1,098
Pennales
Achnanthes 100 200 100 2,494 0 5,486 1.097 399 0
Amphora 499 2.893 200 299 0 0 0 499 0
Cocconeis 200 200 0 0 0 0 200 898 798
Gomphonema 0 0 0 1,097 0 499 200 0 0
Navicula 5,187 10.175 3.890 5.387 698 6.284 4,190 1 8.254 1,895
Nitzschia 3.192 7.382 499 28,928 1,197 9,875 24.239 9,377 3,491
Pinnularia 0 0 0 499 0 100 0 0 0
Rhoicosphenia 0 200 1.895 998 399 399 698 1. 696 100
Surirella 100 0 0 0 0 100 0 0 0
Total Pennales 9,278 21,050 6,584 39.702 2.294 22.743 30.624 31,123 6,284
Total Bacillariophyta 12,670 33,022 7,382 42,295 2,494 25.137 30,824 32,321 7.382
CHLOROPHYTA (Green Algae)
Nonfilamentous
Ankistrodesmus 0 299 299 200 0 100 0 100 0
Chlamydomonas 0 0 100 200 200 299 100 0 100
Chlorella 0 0 0 0 0 0 599 0 0
Lagerheimia 0 100 0 0 0 0 0 0 0
Lobomonas 0 100 0 0 0 0 0 0 0
Oocystis 0 0 0 100 0 0 0 0 0
Pediastrum 0 0 0 0 0 0 0 0 2.993
Scenedesmus 598 798 200 2,394 200 100 798 399 499
Schroederia 0 0 0 299 0 100 100 100 0
Selenastrum 0 0 100 0 0 0 0 0 0
Total Nonfilamentous 598 1.297 699 3.193 400 599 1,597 599 3.592
Filamentous
Cladophora 0 0 0 0 0 698 0 100 0
Stigeoclonium8 3.193 12.070 244.789 5,886 52,170 61.247 8.878 5.586 698
Total Filamentous 3,193 12.070 244.789 5.886 52,170 61.945 8.878 5.686 698
Total Chlorophyta 3.791 13.367 245,488 9.079 52.570 62.544 10,475 6.285 4.290
CRYPTOPHYT A (Cryptomonads)
Chroomonas 0 100 0 0 0 0 0 0 0
Total Cryptophyta 0 100 0 0 0 0 0 0 0
0-1
-------
Table D-1.
(Continued)
Sampling Stations
2 3 4 5 6 7 8 9
o 1,995 0 0 0 0 0 0 0
o 798 0 0 0 0 0 0 0
o 2,195 0 0 0 0 0 0 0
o 4,988 0 0 0 0 0 0 0
CYANOPHYTA (Blue-green Algae)
Nonfilamentous
Chroococcus
Merismopedia
Unidentified cocco ids
Total Nonfilamentous
Filamentous.
Lyngbya
Oscil/atoria
Total Filamentous
Total Cyanophyta
EUGLENOPHYTA (Euglenoids)
Euglena 0 0 100 100 0 0 0 0 0
Total Euglenophyta 0 0 100 100 0 0 0 0 0
Total Periphyton 18,556 55.168 252,970 55.763 55,064 89,876 46,287 40.402 12,570
.Stigeoclonium included both basal and filamentous cells, as well as coccoid green algae that may possibly be growth forms or life stages of
this genus.
bFilamentous blue-green algae were counted in 10-#lm units of length.
1,995
100
2,095
2.095
2.294
1,397
3,691
8.679
o
o
o
o
1 .496
2.793
4,289
4.289
o
o
o
o
599
1,596
2.195
2,195
2,893
2,095
4,988
4,988
1,796
o
1,796
1,796
898
o
898
898
Table D-2. Chlorophyll. and Bioma.. Data and Statistical Results for Periphyton Collected from Natural Substrates in the
Ottawa River. September 1982
Sampling Stations
Parameter 2 3 4 5 6 7 8 9
Chlorophyll a (mg/m2)
Rep 1 13.3 3269 226.8 260.0 160.0 58.8 170.0 594
Rep 2 40.6 230.5 316.6 150.0 140.0 240.0 230.0 228.0 180.0
Rep 3 41.8 210.0 130.0 115.0 1000 180.0 175.0 57.6 50.3
Rep 4 326.9 512.5 2500 46.7 125.0 91.5 122.0 120.0
Mean 31.9 273.6 296.5 193.8 111.7 151.0 166.6 135.9 102.4
Biomass (g/m2)
Rep 1 23.2 71.2 33.8 28.9 18.0 146 20.6 11.5 22.8
Rep 2 28.8 65.7 30.7 17.7 17.6 47.4 24.5 35.7 30.3
Rep 3 19.2 46.5 24.3 38.6 25.0 57.4 22.8 15.9 8.6
Rep 4 17.8 637 54.8 342 17.5 38.8 10.7 29.7 13.2
Mean 22.2 61.8 35.9 29.8 195 39.6 19.6 23.2 18.7
Autotrophic Index (Weber 1973) 971 230 135 176 216 269 119 225 208
Statistical Results: .
Chlorophyll a
F = 6.990 Station" 1 9 5 8 6 7 4 3 2
P < 0.001 Meanc 3.342 4.496 4.616 4.762 4.894 5.064 5.209 5.572 5.790
Biomass
F = 4.371 Station 9 7 5 8 1 4 3 6 2
P < 0.003 Mean 2.818 2.930 2.960 3.044 3.085 3.356 3.535 3562 4.111
"Results based on analysis of variance and Tukey multiple comparison test performed on data transformed with natural logarithms [In (x +
1)). Stations underscored by a continuous line were not significantly different (P > 0.05).
"Stations are listed in order of increasing mean values.
cMeans of transformed data.
D-2
-------
Table D-3.
Ranked Abundance lilting of All Macroinvertebratel Collected from Ottawa River, 21 September 1982
Cumulative
Species Name Number Percent Percent
Simuliidae, L. 5359.617 24.587 24.587
C. (Cricotopus) Bicinctus GRP. 4857.687 22.285 46.872
Cheumatopsyche, L. 2435.019 11.171 58.042
Hydropsyche. L. 1161.009 5.326 63.368
Thienemannimyia, GRP. 1 041 .965 4.780 68.148
Hydropsychidae, L. 913.723 4.192 72.340
Stenelmis L. 769.451 3.530 75.870
Simuliidae. P. 514.019 2.358 78.228
C. (Cricotopus) Tremulus GRP. 455.942 2092 80.319
Chironomidae, P. 423.619 1.943 82.263
Elmidae, L. 383.149 1.758 84.021
Baetis, N. 318.765 1.462 85.483
Empididae, L. 309.830 1.421 86.904
Polypedilum (S.S.) Convictum, L. 221.007 1.014 87.918
Nanocladius. L. 203.400 0.933 88.851
Caenis. N. 188.421 0.864 89.715
Stenelmis, A. 167.923 0.770 90.486
Polypedilum (S.S.) Scalaenum, L. 153.207 0.703 91.189
Bothrioneurum Vejdovskyanum 148.214 0.680 91.869
Ephemeroptera, N. 146.112 0.670 92.539
IMM Tubif with Cap Chaet 142.695 0.655 93.193
IMM Tubif w/o Cap Chaet 121.409 0.557 93.750
Diptera. P. 107.744 0.494 94.245
Berosus, L. 98.809 0.453 94.698
Tricladida 98.284 0.451 95.149
Chironomus. L. 81.728 0.375 95.524
Physel/a 73.056 0.335 95.859
Baetidae. N. 62.807 0.288 96.147
Cricotopus Syvlestris GRP.. L. 60.705 0.278 96.426
Heptageniidae. N. 49.142 0.225 96.651
Rheotanytarsus. L. 45.200 0.207 96.858
Limnodrilus Udekemianus 42.047 0.193 97.051
Stenacron. N. 39.419 0.181 97.232
Glyptotendipes, L. 38.367 0.176 97.408
Tanytarsus, L. 37.579 0.172 97.580
Hydroptila. L. 36.528 0.168 97.748
Simulium. L. 34.951 0.160 97.908
Potamothrix Bavaricus 32.586 0.149 98.058
Ancylidae 31.798 0.146 98.204
Piguetiel/a Michiganensis 26.805 0.123 98.327
Microtendipes. L. 22.600 0.104 98.430
H'eptageniinae, N. 20.498 0.094 98.524
Nais Variabilis 18.921 0.087 98.611
Dero (Dero) Digitata 18.658 0.086 98.697
Psephenus, L. 17.870 0.082 98.779
Hydroptilidae. L. 16.819 0.077 98.856
Dicrotendipes L. 16.556 0.076 98.932
Sphaerium 14.979 0.069 99.001
Trichoptera. L. 11 .563 0.053 99054
Thienemanniel/a, L. 11.563 0.053 99.107
Stenonema. N. 11.300 0.052 99.159
Labrundinia. L. 11.300 0.052 99.210
Ablabesmyia. L. 10.512 0.048 99.259
Dere Funcata 9.986 0.046 99.304
Caenidae N. 9.460 0.043 99.348
Tubifex Tubifex 8.147 0.037 99.385
Cricotopus Tibialis. L. 7.358 0.034 99.41 9
Turbellaria 6.833 0.031 99.450
Gastropoda 6.307 0.029 99.4 79
Nais Communis 6.307 0.029 99 508
Branchiobdellidae 6.307 0.029 99.537
Potamanthus, N. 6.307 0.029 99.566
Argia. N. 5.256 0.024 99.590
Astacidae 4.467 0.020 99.611
Aulodrilus Pigueti 4.205 0.019 99.630
Tricorythidae. N. 4.205 0.019 99.649
Hemiptera U. 4.205 0.019 99.668
Cricotopus, P. 4.205 0019 99.688
D-3
-------
Table D-3.
(Continued)
Species Name
Thienemaniella Nr. Fusca, L.
Corynoneura, L.
P. (Phaenopsectra) L.
Pyralidae, L.
Parachironomus Abortivus Type, L.
Limnodrilus Hoffmeisteri
Nais Bretscheri
Hyalella Azteca
Coenagrionidae, N.
Rhagovelia, A.
Chimarra, L.
Procladius L.
Cryptochironomus L.
Paratendipes Albimanus Type. L.
Chaetogaster Cristallinus
Pristina Longiseta Leidy
Crangonyx .
Zygoptera. N.
Tortricidae, L.
Glossosomatidae, L.
Cricotopus Trifascia. L.
Eukiefferiella. L.
Paratanytarsus, L.
Collembola U.
Orconectes
Helisoma
Enchytraeidae
Elmidae, A.
Berosus, A.
Pseudochironomus L.
Nais Pardalis
Wapsa Mobilis
Rheocricotopus, L.
Pelecypoda
Naididae
Haemopis
Paraleptophlebia. N.
Hemiptera N.
Elodes. L.
Culicidae. P.
Note: L. - Larva
P. ~ Pupa
N. = Nymph
A. - Adult
U. - Unidentified
5.5. Sensu strictu (in the strict sense)
Capitalization of taxa is due to computerized format.
0-4
Number
4.205
3.679
3.153
2.628
2.628
2.365
2.365
2.365
2.365
2.365
2.365
2.365
2.365
2.365
2.102
2.102
2.102
2.102
2.102
2.102
2.102
2.102
2.102
1.577
1.314
1.051
1.051
1.051
1.051
1.051
0.526
0.526
0.526
0.263
0.263
0.263
0.263
0.263
0.263
0.263
Cumulative
Percent
Percent
0.019
0.017
0.Q14
0.012
0.012
0.011
0.011
0.011
0.011
0.011
0.011
0.011
0.011
0.011
0.010
0.010
0.010
0.010
0.010
0.010
0.010
0.010
0.010
0.007
0.006
0.005
0.005
0.005
0.005
0.005
0.002
0.002
0.002
0.001
0.001
0.001
0.001
0.001
0.001
0.001
99.707
99.724
99.738
99.750
99.762
99.773
99.784
99.795
99.806
99.817
99.828
99.838
99.849
99.860
99.870
99.879
99.889
99.899
99.908
99.918
99.928
99.937
99.947
99.954
99.960
99.965
99.970
99.975
99.979
99.984
99.987
99.989
99.992
99.993
99.994
99.995
99.996
99.998
99.999
100.000
-------
Table D-4. Shannon-Wiener Diversity Indices (Cil. Associated Evenness and Redundancy Values, and Community Loss Indices
Calculated on Benthic Data from Ottawa River, 1982
Community
Maximum Minimum Number of Number of Loss
Station Diversity" Evenness Redundancy Diversity Diversity Species Individuals Index"
1 3.8950 0.6800 0.3212 5.7279 0.0242 53 7,124
2 3 6946 0.6481 0.3525 5.7005 0.0106 52 17,094 0.4651
3 1 .7533 0.3507 0.6497 5.0000 0.0030 32 38,808 0.9643
4 2.3552 0.5072 0.4940 4.6439 0.0106 25 7,537 1.3636
5 1.7441 0.3554 0.6451 4.9060 0.0042 30 25.308 1.0769
6 23329 0.4625 0.5384 5.0444 0.0082 33 16.971 0.9667
7 2.2555 0.4210 0.5795 5.3576 0.0047 41 39.595 0.7500
8 3.6047 0.6495 0.3511 5.5546 0.0100 47 16,383 0.5000
9 2.4304 0.5111 0.4892 4.7549 0.0032 27 29,946 1.0435
"Calculated on a log base 2.
"Calculated using Station 1 as reference station.
Table D-6.
List of Fish Species and Familiel Collected from the Ottawa River Near Lima, Ohio, 24-26 September 1982"
Family
Clupeidae
(herring)
Cyprinidae
(minnow)
Scientific Name
Dorosoma cepedianum
Common Name
Gizzard shad
Catastomidae
(sucker)
Cyprinus carpio
Notemigonus crysoleucas
Pimephales promelas
Semotilus atromaculatus
Notropis spilopterus
N. atherinoides
Pimephales notatus
Campostoma anomalum
Notropis stramineus
N. umbratilis
Catastomus commersoni
Moxostoma duquesnei
M. erythrurum
Ictalurus catus
Noturus gyrinus
Fundulus notatus
Carp
Golden shiner
Fathead minnow
Creek chub
Spotfin shiner
Emerald shiner
Bluntn'Ose minnow
Stoneroller
Sand shiner
Redfin shiner
White sucker
Black redhorse
Golden redhorse
White catfish
Tadpole madtom
Blackstripe topminnow
Ictaiurldae
(catfish)
Cyprinodontldae
(killifish)
Centrarchidae
(sunfish)
Ambloplites rupestris
Lepomis cyanellus
L. macrochirus
Micropterus salmoides
Pomoxis annulafls
Lepomis x Lepomis
Etheostoma blennioides
E. caeruleum
E. fIabellare
E. nigrum
Percina maculata
Rock bass
Green sunfish
Bluegill
Largemouth bass
Black crappie
Sunfish hybrid
Greenside darter
Rainbow darter
Fantail darter
Johnny darter
Blackside darter
Percidae (perch)
"Names follow Robins et al. 1980.
D-5
-------
Teble D-S.
Shennan-Wiener Diver.ity Indice. (dl. Allocieted Evenne.. end Redundency Velue.. end Community LOlllndice.
Celculeted on Fi.herie. Dete from Ottewe River. 1982
Number Community
Maximum Minimum of Number of Loss
Station Diversity' Evenness Redundancy Diversity Diversity Species Individuals. Indexc
1 1.6693 0.4511 0.5503 3.7005 0.0093 13 20,295
2 0.9886 0.2530 0.7480 3.9069 0.0055 15 42,884 0.2667
3 0.4478 0.1294 0.8716 3.4594 0.0041 11 41,031 0.5455
4 18444 0.7135 0.3058 2.5850 0.1633 6 295 1 .5000
5 1.3765 0 8685 0.1448 1.5850 O. 1450 3 114 3.6667
6 0 0 12.0000
7 2.7956 0.9319 0.0757 3.0000 0.2996 8 214 1.1429
8 1.1 320 0.3272 0.6744 3.4594 0.0086 11 18,194 0.8000
9 2.3278 0.5480 0.4552 4.2479 0.0294 19 8,917 0.3125
"Calculated on a log base 2.
.Abundance adjusted to number per 465 m2 (sampling area).
cCalculated using Station 1 as reference station.
D-6
.USGPO:
1984-759-102-10650
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