HYDROPOWER STACKING
Prepared by:
U.S. Environmental Protection Agency
Region 3
Philadelphia, Pennsylvania
With the assistance of:
WAPORA, Inc.
Cincinnati, Ohio
(Gary RJ Finni, Ph.D.
Principal Biologist
Robert Stevens, P.E
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HYDROPOVTCR STACKING
Prepared by:
U.S. Environmental Protection Agency
Region 3
Philadelphia, Pennsylvania
With the assistance of:
WAPORA, Inc.
Cincinnati, Ohio
Principal Biologist
Robert Stevens, P.E.
(U\
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TABLE OF CONTENTS
Page
List of Tables iv
List of Figures vi
Acknowledgments viii
1.0 INTRODUCTION 1
2.0 METHODS 6
2.1 EXISTING WATER QUALITY CONDITIONS 6
2.1.1 Summary of Available Data 6
2.1.2 Overview of Water Quality 6
2.1.3 Stream Flows 12
2.2 WATER QUALITY MODELING 15
2.2.1 Model Selection, Parameter Selection, and
Model Start-up 17
2.2.2 Calibration and Verification Procedures .... 28
2.2.3 Impact Analysis 30
2.3 BIOLOGICAL RESOURCES: REVIEW OF LITERATURE 31
2.3.1 Characterization of the Fisheries of the
Study Area 31
2.3.2 Characterization of Spawning Period and
Habitat Requirements 32
2.3.3 Composition and Temporal Occurrence of
Ichthyoplankton Taxa 32
2.3.4 Influence of Low Dissolved Oxygen Concentra-
tions on Fish Eggs, Larvae, and Adults 32
2.3.5 Impacts of Hydropower Plant Operation on
Indigenous Fish Species 33
2.3.6 Impact Analysis 33
3.0 RESULTS 34
3.1 WATER QUALITY 34
3.1.1 Hydropower Facility Development 34
3.1.2 Results of Calibration and Verification .... 36
3.1.3 Projected Water Quality With Hydropower
Development • ••.»«•«»•¦.•»»».. 52
3.2 THE STUDY AREA FISHERY 63
3.2.1 Composition of the Community 63
3.2.2 Relative Abundance of Fishes in the Alle-
gheny, Monongahela, and Ohio Rivers ...... 69
3.3 SPAWNING PERIODS FOR FISHES OF THE ALLEGHENY,
MONONGAHELA, AND UPPER OHIO RIVERS 96
3.4 SPAWNING REQUIREMENTS AND REPRODUCTIVE GUILDS
OF OHIO RIVER FISHES 106
3.5 LARVAL AND JUVENILE FISHES IN THE DRIFT OF THE
OHIO, ALLEGHENY, AND MONONGAHELA RIVERS 119
3.6 DISSOLVED OXYGEN AND ITS INFLUENCE ON FISHES 133
3.7 IMPACTS OF HYDROPOWER PLANT OPERATION ON
INDIGENOUS FISH SPECIES 155
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TABLE OF CONTENTS
Page
4.0 DISCUSSION 157
4.1 EVALUATION OF WATER QUALITY MODEL PREDICTIONS 157
4.2 EVALUATION OF BIOLOGICAL IMPACTS ASSOCIATED WITH
LOW DISSOLVED OXYGEN VALUES 158
5.0 CONCLUSIONS 161
6.0 RECOMMENDATIONS 162
7.0 LITERATURE CITED 163
iii
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LIST OF TABLES
Page
2-1 Water quality data available for the study area 7
2-2 Range of water quality conditions in the study
area rivers 13
2-3 Stream flows used for the hydropower impact analysis ... 16
2-4 Discharge monitoring report data for the five major
point sources in the study area 18
2-5 QUAL II water quality model invariant parameters 25
2-6 QUAL II water quality model reach-variable parameters. . . 27
2-7 Hydraulic parameters selected for the QUAL II water
quality model 29
3-1 Characteristics of study area locks and dams 35
3-2 Reaeration rates predicted by the model (O'Connor-
Dobbins) for verification and calibration 38
3-3 Summary of dam characteristic values computed for
the study area dams AO
3-4 Performance statistics for calibration and verifi-
cation of QUAL II model (dissolved oxygen data) 53
3-5 Flow rates used in impact analysis 55
3-6 Fishes occurring in the upper mainstera of the Ohio
River and lower Allegheny and Monongahela Rivers 64
3-7 Fish collected during Ohio River lock chamber rotenone
studies, Ohio River Miles 0-200, from 1967 through
1983 72
3-8 Fish collected during Allegheny River lock chamber
rotenone studies, Allegheny River Locks No. 3 and 8,
from 1967 through 1983 76
3-9 Fish collected during Monongahela River lock chamber
rotenone studies, Monongahela River Lock No. 2 and
Maxwell Lock, from 1967 through 1983 78
iv
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LIST OF TABLES (continued)
Page
3-10 The results of annual fish sampling near the W.H.
Sammis Plant (Ohio River Mile 53.9) 84
3-11 Reproductive guilds of the 126 species of fish which
reproduced in the Ohio River, and for which infor-
mation on spawning habits is available (after Balon
1975) 115
3-12 Summary of lethal levels of dissolved oxygen for
fishes occurring in the upper mainstem of the Ohio
River and Allegheny and Monongahela Rivers 136
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LIST OF FIGURES
Page
1-1 Lock and dam locations along the Allegheny, Mononga-
hela, and upper Ohio Rivers A
1-2 Delineation of study area 5
2-1 Study area, reaches 19
3-1 Dissolved oxygen predictions and observed data for
QUAL II model calibration of the Ohio River (Data
set 11 July 1983) A3
3-2 Dissolved oxygen predictions and observed data for
QUAL II model calibration of the Monongahela River
(Data set 26 August 1983) AA
3-3 Dissolved oxygen predictions and observed data for
QUAL II model calibration of the Allegheny River
(Data set 28 July 1983) A5
3-A Dissolved oxygen predictions and observed data for
QUAL II model verification of the Ohio River (Data
set 1 August 1983) A7
3-5 Dissolved oxygen predictions and observed data for
QUAL II model verification of the Monongahela River
(Data set 2A July 1980) A8
3-6 Dissolved oxygen predictions and observed data for
QUAL II model verification of the Allegheny River
(Data set 23 July 1981) A9
3-7 Model prediction for Long Terra Monthly Average (LTMA)
flow for the Ohio River 56
3-8 Model prediction for Long Term Monthly Average (LTMA)
flow for the Monongahela River 57
3-9 Model prediction for Long Term Monthly Average (LTMA)
flow for the Allegheny River 58
3-10 Model prediction for Low Flow Expected (LFE) flow for
the Ohio River 60
3-11 Model prediction for Low Flow Expected (LFE) flow for
the Monongahela River 61
3-12 Model prediction for Low Flow Expected (LFE) flow for
the Allegheny River 62
vi
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LIST OF FIGURES (continued)
Page
3-13 The spawning period for the fishes occurring in the
Allegheny, Monongahela, and upper Ohio Rivers 98
3-14 The spawning requirements for fish species occurring
in the Allegheny, Monongahela, and upper Ohio Rivers . . 107
3-15 The temporal distribution of fish larvae and juveniles
in the drift in the Allegheny, Monongahela, and upper
Ohio Rivers 121
3-16 Density of ichthyoplankton collected weekly in net
tows near the New Cumberland Pool, 1976-1982 124
3-17 Weekly percent composition of all tow samples by
dominant families (>10%) near the New Cumberland
Pool, 1976-1982 125
3-18 Density of ichthyoplankton collected weekly in net
tows near the Pike Island Pool, 1978-1982 127
3-19 Weekly percent composition of all tow samples by
dominant families (>10%) near the Pike Island Pool,
1978-1982 129
vii
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ACKNOWLEDGMENTS
Preparation of this assessment would not have been possible without
assistance from many individuals during the acquisition of biological,
water quality, and water quality modeling information, as well as in tech-
nical discussions regarding the scope and direction of the project. In
particular, we acknowledge the following individuals/organizations: Ohio
River Valley Sanitation Commission (ORSANCO); Mr. Mike Korvak, Pittsburgh
District, U.S. Array Corps of Engineers, Pittsburgh, PA; Messrs. William
Pearson and Hugh T. Spencer, University of Louisville, Louisville, KY; Mr.
Michael Miller, University of Cincinnati, Cincinnati, OH; Mr. Robert
Phelps, Ohio Environmental Protection Agency, Columbus, OH; Mr. Mark
Dortch, Waterways Experiment Station, U.S. Array Corps of Engineers, Vicks-
burg, MS; Messrs. Jim Duck and Frank Crist, Louisville District, U.S. Army
Corps of Engineers, Louisville, KY; Mr. William Coffman, University of
Pittsburgh, Pittsburgh, PA; Mr. George Collins, U.S. Environmental Protec-
tion Agency, Region IV, Atlanta, GA; Mr. Mark Anthony, U.S. Array Corps of
Engineers, Cincinnati, OH; Mr. Tom Barnwell, U.S. Environmental Protection
Agency, Region IV, Athens, GA; Mr. Richard Herd, Allegheny Power System,
Greensburg, PA; Mr. Robert Ronowski, U.S. Environmental Protection Agency,
Philadelphia, PA; Mr. Jim Ulanoski, Division of Water Quality, Pennsylvania
Department of Environmental Resources, Harrisburg, PA; Mr. J.K. Cool,
Duquesne Light, Pittsburgh, PA.
viii
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1.0 INTRODUCTION
The Ohio River, one of the Midwest's largest rivers, is formed in
Pittsburgh, Pennsylvania, by the confluence of the Allegheny and Hononga-
hela Rivers. From Pittsburgh, the Ohio River flows generally southwest for
981 miles to its mouth at the Mississippi River near Cairo, Illinois. The
first 40 miles lie wholly within Pennsylvania; for the remainder of its
length, the Ohio River forms the boundary between Ohio, Indiana, and
Illinois to the north, and West Virginia and Kentucky to the south. The
Ohio drains an area of 203,900 square miles of which approximately 95
percent of this area is drained by tributary streams. The drainage area of
the Ohio at its head in Pittsburgh is 19,164 square miles of which the
Monongahela and Allegheny Rivers drain 7,386 and 11,778 square miles,
respectively. Over 20 million people reside within the basin and eight
million reside in areas which drain directly to the mainstem. The largest
metropolitan centers along the Ohio River include Pittsburgh, Pennsylvania,
Cincinnati, Ohio, and Louisville, Kentucky (Ohio River Valley Water Sanita-
tion Commission [ORSANCO] 1984; U.S. Army Corps of Engineers [COE] 1975).
Waters of the Ohio River and its major tributaries are used for power
generation, public water supply, industrial supply, fish and wildlife
habitat, recreation, and navigation. Electric power is generated through-
out the basin primarily through the burning of coal, with the river used as
a source of cooling water. Along the Ohio River, there are 51 intakes for
potable water supply, of which 34 provide water to public or private utili-
ties which serve over three million people. Over 100 industries use the
Ohio River as a source of process water. The Ohio and its major tribu-
taries support a variety of warm water fish species important both to the
sport and commercial catch. In addition to sport fishing, recreational
uses include boating, water-skiing, and swimming. Commercial navigation is
maintained along the Ohio River by a series of 20 locks and dams that are
operated by the COE. These dams maintain a nine foot navigation channel.
Additional locks and dams along the Allegheny and Monongahela Rivers permit
commercial navigation to reach the coal fields in West Virginia and
Pennsylvania (ORSANCO 1984; Leuthart and Spencer 1979; West Virginia
Department of Natural Resources 1983; COE 1975, 1982).
1
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Within the recent past, renewed interest has been kindled in devel-
oping the hydropower potential that currently exists at low-head dams along
many water courses in the United States. The Federal Energy Regulatory
Commission (FERC) reviews permit applications submitted by federal
agencies, utilities, municipalities, and others in the private sector
(licensees). Prior to receiving their permit to construct, the licensee
must prepare an environmental assessment which accompanies the license
application. The environmental assessment addresses the following items:
(1) general description of locale; (2) water use and quality; (3) fish,
wildlife, and botanical resources; (4) historic and archaeological
resources; (5) socioeconomic impacts; (6) geological and soil resources;
(7) recreational resources; (8) aesthetic resources; (9) land use; and (10)
alternative locations, designs, and energy sources. However, these assess-
ments, although complete for a particular hydrosite, do not include an
evaluation of the cumulative impacts of hydropower "stacking" within a
watershed. Such impacts could be significant in the future as increasing
numbers of dams are fitted with electric generating turbines.
Such is the case regarding hydropower development at low-head dams
along the mainstem of the Ohio River and its major tributaries, the
Allegheny and Monongahela Rivers. License applications are pending for all
dams along each of these rivers. From their inception, low-head dams
along the Ohio River and its tributaries were constructed to maintain a
pool suitable for navigation. During high temperature, low flow conditions
of late summer, gates on existing dams are operated by the COE so as to
provide downstream reaeration. However, since each dam is a candidate site
for hydropower development, a potential exists for downstream alterations
in water quality. Each hydroproject proposed for the Allegheny, Mononga-
hela, and Ohio Rivers will be operated as a "run-of-the-river" facility,
and under low flow conditions of late summer and early autumn, each will
have a high water demand. Without the benefit of reaeration that normally
occurs as water passes over the dam or through the gates, the potential
exists for water with low dissolved oxygen to pass from upstream pools
downstream. As increasing numbers of dams are converted for hydropower
production, there is also a potential for cumulative impacts on oxygen
levels to occur, as the oxygen deficit continually increases. Thermal
2
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regimes of navigation pools may be altered as well, for the turbines will
draw and pass cooler bottom water and reduce mixing currently occurring as
water passes over dams.
This study was undertaken to identify and describe the cumulative
impacts of hydropower facility "stacking" on water quality and fishery
resources of the upper Ohio River Basin (Figure 1-1). The project area
includes a 40 mile segment of the mainstem Ohio River and the downstream 15
miles of the Allegheny and the Monongahela Rivers (Figure 1-2). The
objectives of the study are: (1) to define the existing aquatic
biological resources and water quality conditions in the study area, and
(2) to utilize mathematical modeling procedures to predict the potential
impacts of hydropower stacking on water quality and aquatic biological
resources.
Chapter 2.0 describes the methodogies employed in the study. These
include preparing a literature review of baseline water quality conditions
and biological features, and conducting the water quality modeling.
Chapter 2.0 also includes a description of how the results of the water
quality modeling were used to predict impacts on biological resources.
Chapter 3.0 describes the results of the literature review and water
quality modeling. Chapter 4.0 will address potential impacts, and Chapters
5.0 and 6.0 provide the conclusions and recommendations.
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SCALE IN MILES
L/D 8
L/D 7
MONTGOMERY
L/D
EM8WORTH
L/D
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'No
L/D 2
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L/D
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at
MAXWELL L/D
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rouewooHCnr
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L/D 8
PA.
W. VIR. MD.
MORQANTOWN L/D
OPEKISKA L/D
HILDEBRAND L/D
HYOROPOWEB STUDY
LEGEND
lock and dam locations
MAJOR RIVERS ANO STREAMS
CITtE8 AND TOWNS
Figure 1-1. Lock and dam locations along che Allegheny, Monongahela, and upper Ohio Rivers.
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ALLEGHENY RIVER
" SEGMENT 2
SCALE IN MILES
L/D
ALLEGHENY RIVER
SEGMENT 1 \
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MONTGOMERY
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MONONGAHELA RIVER
SEGMENT 1
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MONONGAHELA RIVER
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HYDROPOWER STUDY
LEGEND
LOCK AND DAM LOCATIONS
TYGART
, LAKE
MAJOR RIVERS AND STREAMS
CITIES AND TOWNS
STUDY AREA BOUNDARY
Figure 1-2. Delineation of study area.
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2.0 METHODS
2.1 EXISTING WATER QUALITY CONDITIONS
2.1.1 Summary of Available Data
Water quality in the study area has been evaluated by, among others,
ORSANCO and the Corps of Engineers. Water quality data were obtained for
this study in the form of the: (1) bi-yearly water quality reports pub-
lished by ORSANCO, describing the results of the member sampling; (2) U.S.
Army Corps of Engineers sampling program (AURAS) in conjunction with opera-
tion of the locks and dams along the three rivers; and (3) STORET listings
of all data from the study area. Table 2-1 lists the stations monitored,
the types of data available, and the source from which the information was
available for each river. All data were screened using three criteria—how
recent, how complete, and how comprehensive the data were—to select those
data sets to be used for water quality modeling. The data selected to
calibrate the QUAL II Model were the 11 July 1983 data for the Ohio River;
the 28 July 1983 data for the Allegheny River; and the 26 August 1983 data
for the Monongahela River. The water quality data selected to verify the
accuracy of the calibrated model were the 1 August 1983 data for the Ohio
River; the 23 July 1981 data for the Allegheny River; and the 24 July 1980
data for the Monongahela River. The dissolved oxygen data from the entire
COE data base (years 1976 to 1983) were used for evaluating reaeration
across the locks and dams. These data are included in the discussion of
dam reaeration.
2.1.2 Overview of Water Quality
Water Quality - Long Term. Prior to development in the watershed, the
upper Ohio River was reported to be a clear running stream with a rocky,
sandy bottom. The impact of early development was related primarily to
runoff from land disturbing activities, with sediment loads from tribu-
taries being a major source. Point source loads became significant with
industrial and urban development in the watershed. In conjunction with
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Table 2-1. Water quality data available for the study area.
Location Source: Period - Description
Allegheny River (RM from confluence with Ohio River)
RM 14.7 COE: 8/26/76, 6/30/77, 7/20/77, 8/10/78, 7/12/79,
7/23/81, 7/19/82, 7/22/82, 7/28/83 - temperature,
DO, pH, NH3, TKN, N03, T-P
COE: 7/79, 7/81, 7/82, 7/83 - algal data
RM 14.3 COE: 8/26/76, 6/30/77, 7/20/77, 8/10/78, 7/12/79,
7/23/81, 7/19/82, 7/22/82, 7/28/83 - temperature,
DO, pH, NH3, TKN, NO3, T-P
COE: 7/79, 7/81, 7/83 - algal data
RM 13.3 ORSANCO: 1978-1983 electronic and manual sampling
RM 12.8 COE: 8/26/76, 6/30/77, 7/21/77, 7/29/77, 8/2/77,
8/3/77, 8/10/78, 7/12/79, 7/23/81, 7/22/82,
7/28/83, 9/15/83 - temperature, DO, pH, NH3>
TKN, N03, T-P
RM 9.5 COE: 8/26/76, 6/30/77, 8/10/78, 7/12/79, 7/23/81,
7/22/82, 7/28/83 - temperature, DO, pH
RM 8.8 ORSANCO: 1978-1981 water user
RM 7.4 ORSANCO: 1982-1983 organics data
RM 6.9 COE: 8/26/76, 6/30/77, 7/20/77, 7/29/77, 8/10/78,
7/13/79, 7/23/81, 7/19/82, 7/22/82, 7/28/83 -
temperature, DO, pH, NH3, TKN, N03, T-P
COE: 6/77, 8/78, 7/79, 7/81, 7/82, 7/83 - algal data
RM 6.5 COE: 8/26/76, 6/30/77, 7/20/77, 8/10/78, 7/13/79,
7/23/81, 7/19/82, 7/11/82, 7/28/83 - temperature,
DO, pH, NH3, TKN, N03, T-P
COE: 6/77, 8/78, 7/79, 7/81, 7/82, 7/83 - algal data
RM 3.2 COE: 8/26/76, 7/1/77, 8/10/78, 7/13/79, 7/23/81,
7/22/82, 7/28/83 - temperature, DO, pH
7
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Table 2-1. (continued)
Location Source: Period - Description
Allegheny River (RM from confluence with Ohio River) (cont.)
RM 0.8 COE: 8/1/75, 9/22/75, 8/26/76, 8/30/76, 6/6/77,
7/1/77, 7/20/77, 6/23/78, 7/28/78, 8/10/78,
6/29/79, 7/13/79, 8/13/79, 8/16/79, 7/25/80,
7/24/81, 7/22/82, 8/2/82, 7/11/83, 7/28/83,
8/1/83, 8/26/83 - temperature, DO, pH, NH3,
TKN, N03, T-P
COE: 6/78, 8/78, 6/79, 7/79, 8/79, 7/81, 7/82, 8/82,
7/83, 8/83, 7/84 - algal data
Monongahela River (RM from confluence with Ohio River)
RM 15.1
RM 11.3
RM 11.2
RM 11.0
RM 4.5
RM 0.8
COE: 7/31/75, 6/22/78, 6/28/79, 7/24/80, 8/25/83 -
temperature, DO, pH
COE: 7/31/75, 6/23/78, 6/28/79, 7/24/80, 8/26/83 -
temperature, DO, pH, NH3, TKN, NO3, T-P
COE: 6/78, 6/79, 7/80, 8/83, 7/84 - algal data
STORET: 1975-1978
COE: 7/31/75, 6/23/78, 6/28/79, 7/24/80, 8/26/83 -
temperature, DO, pH, NH3, TKN, NO3, T-P
COE: 6/78, 6/79, 7/80, 8/83, 7/84 - algal data
ORSANCO: 1978-1983 electronic and manual sampling
COE: 8/1/75, 9/22/75, 8/1/75, 9/22/75, 8/27/76,
8/30/76, 6/6/77, 7/1/77, 7/20/77, 9/2/77,
6/23/78, 7/24/78, 8/10/78, 6/29/79, 7/13/79,
8/13/79, 7/25/80, 7/24/81, 7/22/82, 8/2/82,
7/11/83, 7/28/83, 8/1/83, 8/26/83
COE: 7/77, 6/78, 8/78, 6/79, 7/79, 8/79, 7/80, 7/81,
8/82, 7/83, 8/83, 7/84 - algal data
Ohio River (RM from confluence with Allegheny and Monongahela Rivers)
RM 1.0 COE: 8/1/75, 8/27/76, 8/30/76, 6/6/77, 7/1/77,
7/20/77, 6/23/78, 7/24/78, 8/10/78, 6/29/79,
7/13/79, 8/13/79, 7/25/80, 7/24/81, 7/22/82,
8
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Table 2-1. (continued)
Location Source: Period - Description
Ohio River (RM from confluence with Allegheny and Monongahela) (cont.)
RM 1.0 COE: 8/2/82, 7/11/83, 7/28/83, 8/1/83, 8/26/83 -
temperature, DO, pH
COE: 7/82 - algal data
RM 2.0 COE: 6/6/77, 7/24/78, 7/11/83, 8/1/83 - temperature,
DO, pH
RM 3.0 COE: 6/6/77, 7/24/78, 8/2/82, 7/11/83, 8/1/83 -
temperature, DO, pH
RM 4.0 COE: 6/6/77, 7/24/78, 8/2/82, 7/11/83, 8/1/83 -
temperature, DO, pH
RM 4.5 ORSANCO: 1982-1983 organics data
RM 5.0 COE: 6/6/77, 7/24/78, 8/13/79, 8/2/82, 8/1/83 -
temperature, DO, pH
RM 6.0 COE: 9/22/75, 6/6/77, 7/24/78, 8/13/79, 8/2/82,
7/11/83, 8/1/83 - temperature, DO, pH, NH3,
TKN, NO3, T-P
COE: 7/78, 8/79, 8/82, 7/83 - algal data
RM 6.4 COE: 9/22/75,6/6/77,6/24/77,7/24/78,8/13/79,
8/2/82, 7/11/83, 8/1/83 - temperature, DO, pH,
NH3, TKN, NO3, T-P
COE: 7/78, 8/79, 8/82, 7/83 - algal data
RM 7.0 COE: 6/6/77, 7/24/78, 8/2/82, 7/11/83, 8/1/83 -
temperature, DO, pH
RM 9.6 COE: 7/24/78, 8/13/79, 8/2/82, 7/11/83, 8/1/83 -
temperature, DO, pH
RM 13.0 COE: 9/22/75, 6/6/77, 7/24/78, 8/13/79, 8/2/82,
7/11/83, 8/1/83 - temperature, DO, pH, NH3,
TKN, NO3
COE: 6/77, 8/79, 8/82, 7/83 - algal data
9
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Table 2-1. (continued)
Location Source: Period - Description
Ohio River (RM from confluence with Allegheny and Monongahela) (cont.)
RM 13.5 COE: 9/22/75, 6/6/77, 7/24/78 -b temperature, DO, pH
COE: 8/13/79, 8/2/82, 7/11/83, 8/1/83 - temperature,
DO, pH, NH3, TKN, N03, T-P
COE: 8/79, 8/82, 7/83
RM 15.8 ORSANCO: 1978-1983 electronic and manual sampling
RM 17.0 COE: 7/24/78, 8/13/79, 8/2/82, 7/11/83, 8/1/83 -b
temperature, DO, pH
RM 23.5 COE: 9/22/75, 6/6/77, 7/24/78, 8/13/79, 8/2/82,
7/11/83/ 8/1/83 - temperature, DO, pH
RM 28.1 COE: 6/6/77, 7/24/78, 8/14/79, 8/3/82, 7/11/83 -
temperature, DO, pH
RM 31.3 COE: 9/23/75, 6/7/77, 7/25/78, 8/14/79, 8/3/82,
7/12/83, 8/2/83 - temperature, DO, pH, NH3,
TKN, NO3, T-P
RM 32.0 COE: 9/23/75, 6/7/77, 7/25/78 - temperature, DO, pH
COE: 8/14/79, 8/2/82, 7/12/83, 8/2/83 - temperature,
DO, pH, NH3, TKN, NO3, T-P
RM 33.1 COE: 6/7/77, 7/25/78, 8/14/79, 8/3/82, 7/12/83, 8/2/83
- temperature, DO, pH
RM 38.0 COE: 7/12/83, 8/2/83 - temperature, DO, pH
RM 40.2 ORSANCO: 1978-1983 electronic and manual sampling
RM 40.3 COE: 6/7/77, 7/25/78, 8/14/79, 8/3/82, 7/12/83, 8/2/83
- temperature, DO, pH
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Table 2-1. (continued)
References:
COE 1. U.S. Army Corps of Engineers, Pittsburgh District,
Auras Raw Data Report for Water Quality, 9 October
1984
COE 2. U.S. Army Corps of Engineers, Pittsburgh District
STORET: Water quality data retrieval
ORSANCO: 1980. 1982, 1984
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-------
these changes, the development of navigation dams along the upper Ohio
altered the velocity profile in the river.
These general factors led to a degraded water quality condition in the
upper Ohio River in the late 1950's and 1960's. The passage of PL 92-500,
with the emphasis on uniform effluent limited point source controls for
municipal and industrial discharges, resulted in a high level of point
source control. Historical water quality trends have been analyzed by
ORSANCO starting in 1977 (0RSANC0 1980). These analyses show that since
1961, pH and D.O. in the upper river have been improving in terms of
meeting recommended criteria. Trends show improvement for 1964-1975 for
chlorides, hardness, sulfate, and turbidity. Problems were still increas-
ing through 1979 for mercury and fecal coliform bacteria.
Present Water Quality. The range in water quality parameter values
for the data sets used in modeling are summarized in Table 2-2. These
data reflect generally good water quality and are consistent with the long
term results reported by ORSANCO (ORSANCO 1980, 1982, 1984). In particu-
lar, the dissolved oxygen levels in the river in the study area are near
the saturation limit, generally greater than 80 percent of the saturation
level. At several stations, a low dissolved oxygen was measured near
bottom, possibly indicating a local area of stratification. However, the
data almost always exhibited a uniform temperature and dissolved oxygen
distribution at each station, although the surface sample often was
slightly higher in temperature and dissolved oxygen than the remaining
water column samples.
2.1.3 Stream Flows
It was considered that critical conditions for dissolved oxygen would
be the July to September period, where low flow and high temperatures are
common. Flow records for the past several years for these months were
reviewed to identify the approximate critical conditions. The data
reviewed included reports by ORSANCO (ORSANCO 1980, 1982, 1984), the gage
data at several locations (Monongahela at Braddock, PA; Allegheny River at
New Kensington, PA; Ohio River at Sewickley, PA; and Beaver River at Beaver
12
-------
Table 2-2. Range of water quality conditions in the study area rivers.
Location
Period
Temperature
nh3
1
TKN
nifi/1
no3-no2
mg/1
Total-P
Pg/1
Chlorophyll a
ur/i
Allegheny River
RM 14.7
(ACP 1002)
7/28/83
7/22/82
7/23/81
26.7-30.3
26.9-30.9
25.1-25.9
7.0-7.1
6.5-6.9
6.8
<0.1-0.2
0.1-0.2
<0.1-0.1
0.6-0.8
0.2-0.3
0.2-0.A
1.0-16.7
0.3-0.4
0.4-0.8
10-20
<10
<10
3.8-4.0
5.6
1.8
RM 14.3
7/28/83
28.1-28.3
7.7-7.8
<0.1
0.4
0.3
<10
4.2
(ACP 1201)
7/22/82
28.0-28.3
7.0-7.7
0.1-0.2
0.2
0.3-0.4
<10
—
7/23/81
25.4-25.6
7.6
<0.1
0.3
0.4
<10
0.9
RM 6.9
7/28/83
27.9-28.1
7.6-8.0
<0.1-0.1
0.5-0.6
0.4
10-20
5.5-6.0
SHP 1002)
7/22/82
27.9-28.6
7.0-7.3
0.1
0.2
0.4
<10
5.6
7/23/81
25.2-25.3
7.3
<0.1
<0.1
0.5
<10
1.6
RM 6.5
7/28/83
27.9-28.0
7.98
<0.1
0.6
0.4
20
6.1
(SHP 1201)
7/22/82
27.9-28.0
7.6-7.8
0.1
0.2
0.4
<10
4.5
7/23/81
25.3
8.3-8.4
<0.1
<0.1
0.6
<10
1.5
RM 0.8
7/28/83
27.4-27.8
7.7-8.8
<0.1
0.3
0.4
<10
6.7
(ALC 3001)
7/22/82
27.7-28.1
7.1-7.4
0.1-0.2
0.2-0.3
0.4
<10
7.0-7.2
7/24/81
25.1
7.8-8.0
0.1
0.3
0.5
<10
1.8
Monongahela River
RM 11.3
8/26/83
28.4-28.6
6.0-6.7
<0.1
0.7
1.1
<10
13.2
(BDP 1002)
7/24/80
24.2-24.7
7.0-7.3
0.1
0.5
1.1
70
—
6/28/79
24.2-25.9
7.1-7.6
0.3
0.3
0.8-0.9
30-40
RM 11.0
8/26/83
28.7-29.1
6.5-6.6
<0.1
0.6
1.2
<10
14.0
(BDP 1201)
7/24/80
24.2-24.3
7.2-7.8
0.1
0.5
1.1
110
—
6/28/79
26.8-27.0
7.3-7.4
0.4
0.4
0.9
30
—
RM 0.8
8/26/83
28.6-28.8
5.6-6.9
0.3
0.6
1.1
<10
14.2
(MDN 3001)
7/25/80
24.4-24.5
6.1-6.6
0.2
0.7
1.4
70
—
6/29/79
25.2-25.5
6.2-6.4
2.2-2.8
2.8
1.2
30
—
-------
Table 2-2. (continued)
Temperature
D.O.
NH3
TKN
NO^-NO-
Total-P
Chlorophyll
Location
Period
°C
mg/1
mg/1
mg/1
mg/1
Pg/1
Pg/1
Ohio River
RM 1.0
8/1/83
26.4-28.0
6.7-7.5
0.1
0.6
<0.1
<10
—
(EMP 1012)
7/11/83
24.6-24.7
8.2-9.0
—
—
—
—
—
8/2/82
25.0-25.5
6.9-7.4
0.3
0.8
0.7
<10
—
RM 6.0
8/1/83
27.6-27.8
6.8-7.2
0.2
0.8-0.9
<0.1
<10
8.4
(EMP 1002)
7/11/83
24.1-24.4
7.1-8.2
0.2
0.6
0.7-0.8
20
9.3-9.7
8/2/82
25.3-25.6
6.8-7.1
0.4-0.6
1.1-1.2
0.6
<10
8.2-8.4
RM 6.4
8/1/83
27.7
7.7-8.0
0.3
0.8
<0.1
10
10.2
(EMP 1201)
7/11/83
24.3-24.4
8.1-8.8
0.2
0.5
0.7
20
9.3
8/2/82
25.4-25.5
6.7-7.0
0.3
1.0
0.6
<10
8.2
RM 13.0
8/1/83
27.5-27.6
7.1-7.7
0.2-0.3
0.6
0.6-0.7
10
—
(DDP 1002)
7/11/83
24.5-26.0
7.3-8.5
<0.1-0.1
0.5
0.7
<10-10
2.1-13.2
8/2/82
25.2-25.9
6.6-7.2
0.2
/
0.7-0.9
0.6
<10
8.1
RM 13.5
8/1/83
27.6
8.5-8.7
0.5
0.5
<0.1
10
—
(DDP 1201)
7/11/83
24.9-25.2
8.0-8.2
0.1
0.4
0.7
20
11.6
8/2/82
25.3-25.5
7.2-7.5
0.2
0.8
0.6
<10
8.4
RM 31.3
8/2/83
27.1-27.2
7.0-7.6
0.5
0.7-0.8
0.3
10-80
14.7
(MDP 1002)
7/12/83
24.6-24.9
7.1-8.4
0.3
0.7-0.8
1.0
<10-10
10.6-12.8
8/3/82
26.1-26.2
3.4-7.8
0.2
0.7
0.7
<10
14.8
RM 32.0
8/2/83
27.3
8.4-8.7
0.4
0.8
0.3
10
11.1
(MDP 1201)
7/12/83
24.8-24.9
8.2-8.7
0.3
0.7
1.0
20
10.8
8/2/82
26.1-26.2
5.2-8.8
0.2
0.8
0.7
<10
RM 40.3
8/2/83
27.3-27.4
8.0-8.5
—
—
—
—
7/12/83
24.8-25.1
8.2-8.9
—
—
—
—
8/3/82
26.1-26.2
5.0-8.2
—
—
—
—
-------
Falls, PA), and FERC applications for Montgomery Island Lock and Dam (L/D),
Emsworth L/D, and Dashields L/D (C.E. Maguire 1983a, 1983b; C.T. Main
1984). The development of flows at specific recurrence intervals was not
included in this study. Rather, the stream flows for the impact modeling
were selected to evaluate the typical condition (i.e., the long term
monthly average, LTMA) and the expected worst case situation (i.e., lowest
flow expected, LFE). The LTMA was developed for the Ohio River and
Allegheny River using the information in the ORSANCO reports, with a flow
balance used to estimate the flow for the Monongahela River headwater. The
LFE was developed in a similar manner using the conditions observed in
September 1983. These data are presented in Table 2-3.
2.2 WATER QUALITY MODELING
Subsequent to reviewing the existing data base, initial values for the
QUAL II model parameters were selected. Calibration involved selecting the
most complete data set to serve as a target and adjusting model parameters
to reflect these data. This included: (1) estimating headwater condi-
tions; (2) estimating point source loads to be consistent with in-stream
pollutant levels; (3) developing hydraulic conditions; and (4) identifying
target levels for model predictions (mainly dissolved oxygen, but also
including BOD, ammonia, and chlorophyll a). Once the predictions matched
the observed condition reasonably well, a new set of modeling conditions
was established to verify the model calibration. The model was run using
the parameters as adjusted during calibration and the conditions of the
verification data set. The predicted dissolved oxygen values were compared
to the observed values for the calibration and verification to determine
the relative accuracy of the individual runs.
During the calibration/verification of the model, a series of runs
were performed under several hydropower development scenarios. These runs
were used to develop the range of water quality impacts expected due to
development of each lock and dam as well as the cumulative impacts of
complete development.
15
-------
Table 2-3. Stream flows used for the hydropower impact analysis.
Location
(1) HW Allegheny River
(2) HW Monongahela River
(3) Confluence/HW Ohio
(4) ALCOSAN WWTF
(5) Beaver River
(6) DS Ohio
Long Term
Monthly Average
Flow
(cfs)
4,730 (a)
3,990 (c)
8,720 (a)
300 (b)
1,410 (a)
10,430 (c)
Lowest Flow
Expected
(cfs)
1,890 (c)
1,440 (d)
3,330 (d)
300 (b)
670 (d)
4,300 (c)
(a) Based on data by ORSANCO
(b) Based on permit limitation
(c) Computed by flow balance: (1) + (2) = (3); (3) + (4) + (5) = (6)
(d) Based on lowest flow observed September 1983
16
-------
2.2.1 Model Selection, Parameter Selection, and Model Set-up
The water quality model selected was the Vermont version of the QUAL
II model (WAPORA 1984a). This is a steady-state, one dimensional model
that uses the classical Streeter-Phelps approach for carbonaceous BOD
oxidation, ammonia oxidation, and reaeration. In addition, the model will
predict the level of algal activity in the water body, including photosyn-
thetic activity and respiration demand. The model includes the capability
to predict reaeration at dams at various levels of flow. This capability
was used in the modeling effort to simulate various levels of hydropower
diversion of water through the turbine. A major disadvantage with QUAL II
is that it requires a great amount of data for proper calibration and
verification. In this study, the existing water quality data were quite
extensive, allowing a fairly good basis for using the QUAL II model.
The QUAL II model simulates the river as a series of reaches, each
reach selected to represent areas of similar hydraulic and hydrologic
features. The reaches are subdivided into a number of computational
elements, each representing a length of stream to which the model equations
are applied. The physical layout of the rivers including model reaches is
presented in Figures 1-2 and 2-1. The computational element length
selected was 0.2 mile. This resulted in a model with 350 computational
elements (75 each for the Allegheny and Monongahela Rivers, and 200 for the
Ohio River). Each of the six locks and dams in the study area was there-
fore defined as a reach of 0.2 mile length (i.e., one computational
element), which provided very good definition of the influence of the dams
on water quality.
The point source discharges to the river were reviewed to determine
those that should be included in the model. The factors considered were a
flow greater than 10 mgd, and high BOD or ammonia levels. The point source
characteristics data were obtained from USEPA and from conversations with
dischargers (Gearing,personal communication). The sources that met these
criteria are listed in Table 2-4. Based on the load from these sources,
only the A1C0SAN source (Allegheny County Sanitation Authority) was
included in the model setup. The discharges from the three Duquesne power
plants were considered to not represent a major organic load on the river.
17
-------
Table 2-4. Discharge monitoring report data for the five major point
sources in the study area.
Average3 Average3 Average3
Flow BODc NHo
Facility (mgd) (mg/1) (mg/l)
ALCOSAN 156.8 13 6.6b
Duquesne Mifflin 250 NA NA
Duquesne Light Co. 229.6 NA NA
Duquesne Light Co.
Cheswick 317 NA NA
Neville Coke & Iron 13.5 NA 3.05
aSource October 1984 discharge monitoring report.
^Calculated based on observed BOD5 average, BODp and percent
nitrogenous demand input to model.
18
-------
SCALE IN MILES
FORD
, CITY
L/D 6
R.M. 36.3
L/D 4
R.M. 24.2
R.M.
40
L/D 3
R.M. 14.5
NEW
KENSINGTON
^ *N
R.M.
30
28
NATRONA
HEIGHTS
L/D 5
R.M. 30.4
R.M.
20
R.M.
U3
,76,
CITY OF
PITTSBURG
L/D 2
R.M. 6.7
AND
VACINITY
's,, R.M.
START OF
STUDY
LEGEND
LOCK AND DAM LOCATIONS
©R.M.
RIVER MILE POINTS
STUDY AREA BOUNDARY
RIVERS, STREAMS
URBAN AREA BOUNDARIES
MAJOR HIGHWAYS
STUDY REACHES
HYDROPOWER STUDY
ALLEGHENY RIVER - SEGMENT 1
Figure 2-1. Study area reaches
-------
Irv-L-J
SCALE IN MILES
L/D 8
R.M. 52.6
L/D 9
R.M. 62.2
KITTANNING
FORD
L/D 7
R.M. 45.7
PARKER
END OF
STUDY
R.M. 85.0
0 R.M.
-ooo
LEGEND
LOCK AND DAM LOCATIONS
RIVER MILE POINTS
STUDY AREA BOUNDARY
RIVERS, STREAMS
URBAN AREA BOUNDARIES
MAJOR HIGHWAYS
Figure 2-1. (continued)
HYDROPOWER STUDY
ALLEGHENY RIVER - SEGMENT 2
-------
CITY
M °F
^ PITTSBURGH
START OF'
" STUDY vi
^R.M. 0
AND VAC NITY
L/D 3
R.M. 23.8
R.M.
40
/
L/D 4
R.M. 41.5
0 5
KHZHZ]
SCALE IN MILES
RIVER
R.M.
50
R.M.
60 ,
H
©R.M.
OO-Q-
3
LEGEND
LOCK AND DAM LOCATIONS
RIVER MILE POINTS
STUDY AREA BOUNDARY
RIVERS, STREAMS
URBAN AREA BOUNDARIES
MAJOR HIGHWAYS
STUDY REACHES
HYDROPOWER STUDY
MONONGAHELA RIVER - SEGMENT 1
MAXWELL
L/D
R.M.6I.2
-J
I'ifcure 2-1. (continued)
-------
brwtrl
SCALE IN MILES
LAKE
LYNN
119'
R.M
119) '"MORGANTOWN
'—V t
t\k ^
119]
HILDEBRAND L/D
R.M. 108.0
R.M.
100
R.M.
80
L/D 8
R.M. 90.8
R.M.
L 110
L/D 7
R.M. 85.0
R.M.
70
MORGANTOWN L/D
R.M. 102.0
OPEKISKA L/D
R.M. 115.4
ENO OF
STUDY
R.M. 117.0
LEGEND
LOCK AND DAM LOCATIONS
©R.M.
RIVER MILE POINTS
STUDY AREA BOUNDARY
RIVERS, STREAMS
URBAN AREA BOUNDARIES
HYDROPOWER STUDY
MAJOR HIGHWAYS
MONONGAHELA RIVER - SEGMENT 2
Figure 2-1. (continued)
-------
SCALE IN MILES
22
23
24
R.M.
,2°
120
30
26
MONTGOMERY ISLAND L/D
R.M. 31.7
I END OF
\ STUDY
\ R.M. 40 0
.79.
EMSWORTH L/D
R.M. 6.2
o.
DASHIELDS L/D
R.M. 13.3
START OF
STUDY j
\ R.M. 0J
LEGEND
179,
LOCK AND DAM LOCATIONS
n PITTS.
©R.M.
RIVER MILE POINTS
y AND
VACINITY
STUDY AREA BOUNDARY
RIVERS, STREAMS
URBAN AREA BOUNDARIES
•0""0~0"* MAJon HIGHWAY
_2_ STUDY REACHES
HYDROPOWER STUDY
OHIO RIVER SEGMENT
Figure 2-1. (continued)
-------
The Neville Coke and Iron discharge was not included because at the flow
and limits indicated, the impact on the river would be expected to be
minor. The model set-up also included the Beaver River tributary to the
Ohio River. This was modeled as a point source to the main stem.
The model parameters are established on a system-wide basis (invariant
parameter) and on a reach-specific basis. The invariant parameters (and
their normal range) selected are shown in Table 2-5; the values selected
were based on a review of the data for the study area and sensitivity
analyses (for several parameters) with the selection of a value consistent
with the data.
The model parameters established on a reach-specific basis are identi-
fied in Table 2-6. These values were initially established based on
published guidance for the QUAL II model (WAPORA 1984; USEPA 1980) and a
review of the published reports and data for the rivers. The values for
selected parameters were developed during the sensitivity analyses
performed for model calibration.
Another model set-up activity included the development of hydraulic
parameters to predict the velocity, depth, and width of the rivers. The
QUAL II model uses equations of the form:
(characteristic) = (coefficient) x (flow) (exponent)
where:
characteristic = velocity (ft/sec), width (ft), or depth (ft)
coefficient = value (a for velocity, c for depth, and e for width),
such that
a + c + e = 1.0
exponent = value (b for velocity, d for depth, and f for width),
such that
b x d x f = 1.0
flow = river flow, cfs
24
-------
Table 2-5* QUAL II water quality model Invariant parameters.
N9
CS1
Variable
a2
H
ALPIIA1
Description
N content of algae biomass
ALPHA2 P content of algae biomass
ALPHA3 0 production by algae (photosynthesis)
ALPHA4 0 uptake by algal (respiration)
ALPHA5 0 uptake by NH3 oxidation
ALPHA6 0 uptake by NO2 oxidation
Po
ALGDRT
Algal death rate
p
RESPRT
Algal respiration rate
P1
PREFN
Algal preferential uptake of NH3
p2
ALGNRT
Algal-N to organic-N decay rate
'Sin
CKN
Half saturation constant for N
kmp
CKP
Half saturation constant for P
04
CKPORG
Organic-P decay rate
*5
SVP0RG
Organic-P settling rate
u
max
GROMAX
Maximum specific growth rate for algae
Units
Recommend Value
Range
Value
Selected
mg N
mg
A
mg
P
mg
A
mg
0
mg
A
mg
0
mg
A
mg
0
mg
N
mg
0
1/day
1/day
(no units)
1/day
rag/1
mg/1
1/day
1/day
1/day
0.07 - 0.09 0.09
0.01 - 0.02 0.02
1.4 - 1.8 2.0
1.6 - 2.3 1.4
3.0 - 4.0 3.4
1.0 - 1.14 1.17
0.024 - 0.24 0.02
0.05 - 0.5 0.4
0.0 - 0.9 0.8
0.11 0.11
0.01 - 0.20 0.20
0.01 - 0.05 0.05
0.1 - 0.7 0.6
0.001 - 0.10 0.001
1.0 - 3.0 2.0
-------
Table 2-5. (continued)
Variable
kML
A .
Description
CKL Half saturation constant for light
EXALG Algal light extinction coefficient
Units
Ly/rain
1/ft
yg Chl-a/L
Recommend Value
Range
0.02 - 0.10
0.005 - 0.02
Value
Selected
0.03
0.05
IS>
O)
-------
Table 2-6. QUAL II water quality model reach-variable parameters.
Variable
Description
Units
Recommend Value
Range
Value
Selected
*10
CK1
Laboratory deoxygenation rate
1/day
0.02 - 3.4
0.01
BACT
BACT
Bed activity coefficient
(no units)
0.10 - 0.60
0.03
k2
CK2
Reaeration rate
1/day
0.0 - 100.0
variable
k3
CK3
Settling rate for CBOD
1/day
-0.36 - 0.36
0.0
k4
CK4
Benthlc O2 demand
rag 0
ft-day
highly variable
0
a
o
ALPHA
Mass ratio of chl-a to algae
ng chl-a
mg A
10 - 100
10
ai
ALGSET
Settling rate for algae
ft/day
0.5 - 6.0
variable
a2
SDIS
Benthos source rate for dissolved P
mg P
day-ft
highly variable
0
°3
SNH3
Benthos source rate for NH3
rag N
day-ft
highly variable
0
81
CKNH3
NH3 oxidation rate
1/day
O
O
•
1
0
•
0
0.10
B2
CKN02
NO2 oxidation rate
1/day
0.20 - 2.00
2.0
b3
CKNH2
Organic-N hydrolysis rate
1/day
0.01 - 1.00
0.1
DKP
Dissolved-P removal rate
1/day
0.01 - 1.00
0.05
*o
EXCOEF
Non-algal light extinction coefficient
1/ft
variable
variable
-------
For the Ohio River reaches, the coefficients and exponents for
velocity were selected based on a regression equation developed by ORSANCO.
The values for the Allegheny and Monongahela Rivers were selected to
predict a velocity considered to be reasonable based on mass balance
considerations. The width parameters were selected to predict channel
widths reported for the rivers. The depth parameters also were selected to
match reported depths. The values were selected on a reach-specific basis,
and they are included in Table 2-7.
The model set-up also requires specifying the climatic condition for
each run (light intensity, hours of daylight) and headwater conditions.
These values were developed for each run to reflect the conditions being
modeled.
2.2.2 Calibration and Verification Procedures
The model was calibrated using three data sets: Ohio River reaches
with 1 August 1983 data; Allegheny River with 28 July 1983 data; and
Monongahela River with 26 August 1983 data. This involved three separate
model set-ups, with adjustment of model parameters as required to match the
observed data as closely as possible. This calibration approach was
selected because there was no consistent data set applicable to the entire
study area. There were no major problems encountered with this approach.
The model verification also was performed using the segmented
approach. The Ohio River reaches in the calibrated QUAL II model were
verified using a 11 July 1983 data set, the Allegheny River using a 23 July
1981 data set, and the Monongahela River using a 24 July 1980 data set.
An evaluation of the model verification results versus calibration results
was performed by an error analysis. This involved comparing the predicted
dissolved oxygen to the observed level at each station where data were
available. The average error, absolute value average error, and error
standard deviation were computed for the calibration and verification runs
(u§ing each station as a replicate). This analysis does not establish an
absolute level of confidence in the model, but serves to characterize
relative performance.
28
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Table 2.7. Hydraulic parameters selected for the QUAL II water quality
model.
Velocity
Depth
River
-Reach-Mile
a
b
c
d
Allegheny River
1
15.0-14.6
0.007
0.78
2.03
0.197
2
14.6-14.4
0.007
0.78
2.03
0.197
3
14.4-10.6
0.007
0.78
2.03
0.197
4
10.6-6.8
0.007
0.78
2.03
0.197
5
6.8-6.6
0.007
0.78
2.03
0.197
6
6.6-2.8
0.007
0.78
2.03
0.197
7
2.8-0.0
0.007
0.78
2.03
0.197
Monongahela River
8
15.0-11.2
0.0013
0.702
1.18
0.266
9
11.2-11.0
0.0013
0.702
1.18
0.266
10
11.0-7.2
0.0013
0.702
1.18
0.266
11
7.2-3.4
0.0013
0.702
1.18
0.266
12
3.4-0.0
0.0013
0.702
1.18
0.266
Ohio
River
13
0-3.8
0.003
0.796
5.25
0.156
14
3.8-6.0
0.003
0.796
5.25
0.156
15
6.0-6.2
0.003
0.796
5.25
0.156
16
6.2-20.0
0.004
0.790
4.87
0.153
17
10.0-13.2
0.004
0.790
4.87
0.153
18
13.2-13.4
0.004
0.790
4.87
0.153
19
13.4-17.2
0.004
0.790
4.87
0.153
20
17.2-21.0
0.004
0.790
4.87
0.153
21
21.0-24.8
0.004
0.790
4.87
0.153
22
24.8-28.6
0.004
0.790
4.87
0.153
23
28.6-31.6
0.004
0.790
4.87
0.153
24
31.6-31.8
0.004
0.790
4.87
0.153
25
31.8-35.6
0.003
0.796
5.25
0.156
26
35.6-39.0
0.003
0.796
5.25
0.156
27
39.0-40.0
0.003
0.796
5.25
0.156
29
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2.2.3 Impact Analysis
The impact analysis was performed using the calibrated and verified
model to predict dissolved oxygen levels in the rivers under several hydro-
power development scenarios. The model was run for all three rivers in
each analysis. The conditions at each lock and dam were modified to
reflect a separate development scenario.
The environmental conditions selected for the analysis included hot,
low flow conditions expected during July-September. The river flow and
temperature were selected by reviewing the data available from ORSANCO, the
Pittsburgh District Corps of Engineers, STORET, the Pennsylvania Department
of Environmental Resources, and FERC applications for hydropower develop-
ment at the Dashields L/D, Emsworth L/D, and Montgomery L/D. The condi-
tions selected for analysis correspond to an expected LTMA flow, and a LFE.
These were developed by inspection of the available data and were not
developed from an independent review of the gage data.
The low-head dam retrofit to hydropower was simulated by using QUAL II
model features for dam reaeration. The literature for dam reaeration
predictive methods and theory was reviewed. This review indicated that the
formula included in the Vermont version of the QUAL II model followed the
form of the British dam formula and is widely accepted. Therefore, the
existing upstream/downstream dissolved oxygen data for each lock and dam
were evaluated to establish the parameters required for the dam reaeration
formula. The hydropower conversion was modeled as a bypass of flow around
the dam (i.e., through the turbine with no reaeration rather than across
the dam with reaeration). Bypasses of zero percent, 50 percent, and 100
percent flow were modeled to establish a range of impacts. An intermediate
bypass level can be inferred from these results by interpolation.
The impact analysis included the evaluation of the calibrated model at
the three levels of hydropower development (i.e., zero, 50 percent, and 100
percent of flow bypassing the dam) for the LTMA and LFE. The sensitivity
of the model parameters selected with respect to the calibration and the
impact analysis results was also analyzed. The sensitivity analyses
30
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addressed (see Tables 2-5 and 2-6 for variable definition) were: (1) oxi-
dation rates for biochemical oxidation demand and ammonia (CK^> CKNH3);
(2) reaeration rate for the river (CK2); and (3) algal parameters (light
extinction, EXALG and EXCOEF; oxygen production and respiration rates,
ALPHA 3 and ALPHA A; growth rate, GROMAX; and light saturation constant,
CKL). The effect of these sensitivity runs is discussed in Chapter 3.
2.3 BIOLOGICAL RESOURCES: REVIEW OF LITERATURE
2.3.1 Characterization of the Fisheries of the Study Area
The fisheries resource of the Ohio River varies considerably from its
origin in Pittsburgh to its mouth in Cairo, Illinois. The fisheries of the
study area—the upper Ohio River and lower reaches of the Allegheny and
Monongahela Rivers—were characterized based upon information obtained from
the following sources:
0 Regional fisheries studies;
0 Utility prepared 316(a) and 316(b) and related documents;
0 Biological resource characterizations contained in F.E.R.C.
Exhibit E's for study area low-head dams;
0 U.S. Army Corps of Engineer District Offices;
0 Ohio River Valley Water Sanitation Commission;
0 State agencies; and
0 University faculties.
Although this review focuses on the study area, information for the upper
260 miles of the Ohio River was included. The reasons for this are
two-fold: (1) to increase the information available, especially for
ichthyoplankton, and (2) to include species presently not in the study
area, but whose distribution may include the study area as water quality in
the upper basin continues to improve. Changes in community composition
through time were noted where such comparisons could be made.
31
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2.3.2 Characterization of Spawning Period and Habitat Requirements
Subsequent to describing the composition of the fish community in the
study area, each species' spawning period, i.e., season, and specific
habitat requirements, were characterized. It was anticipated that the high
temperature-low flow period of each year, and possibly attendant low
dissolved oxygen concentrations, would be that period most critical to
successful fish spawning and egg and larval survival. Species spawning
prior to or after the August-September period should encounter temperature
and dissolved oxygen conditions nearer their optima for survival and
growth. Spawning habitat requirements also vary considerably among
species. Characterization of spawning habitat requirements will provide
insight to the species that could be expected to spawn in the Ohio River,
and where in the river they might spawn, (i.e., shoreline, mid-river,
etc.).
2.3.3 Composition and Temporal Occurrence of Ichthyoplankton Taxa
Although several species of fish potentially spawn in the upper Ohio
River, actual utilization is best indicated by documentation of the
occurrence of various taxa of ichthyoplankton in samples collected from the
river. Data concerning the composition and temporal occurrence of each
taxon were compiled from 316(b) demonstration documents prepared for
utilities with generating facilities along the Allegheny, Monongahela, and
Ohio Rivers. These data were then used to supplement information presented
in several annual "Ohio River Ecological Research Program" reports prepared
by WAPORA, Inc. (1973-1981) and Geo-Marine, Inc. (1982, 1983).
2.3.4 Influence of Low Dissolved Oxygen Concentrations on Fish Eggs,
Larvae, and Adults
A potential impact associated with retrofitting low-head dams for
hydropower production is a reduction of reaeration and depressed dissolved
oxygen concentrations at the downstream face of the dam. To assess the
potential for biological impacts (i.e., reduced spawning, embryo or larval
mortality, or exclusion), a review of literature was undertaken that
focused on survival and behavior of fish at depressed dissolved oxygen
32
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concentrations. Literature pertinent to the fishery of the Ohio River is
also included. An extensive literature base for salmonids exists but was
not considered because the Ohio is a Midwestern river with a warm-water
fishery. Doudoroff and Shumway's 1970 comprehensive review of the
dissolved oxygen requirements of freshwater fishes served as the initial
source for this overview.
2.3.5 Impacts of Hydropower Plant Operation on Indigenous Fish Species
Hydropower facilities impinge and entrain fish occurring in the source
water. The emphasis of this portion of the literature review will be to
focus on the types of injuries sustained by fish passing through hydro-
facilities, and on mortality rates sustained by warm-water species passing
through bulb-turbine equipped hydrofacilities.
2.3.6 Impact Analysis
The water quality modeling results will project levels of dissolved
oxygen through the study reach. If, and where, dissolved oxygen levels are
below accepted water quality standards for this parameter (5.0 mg/1), then
the projected levels will be used to define impacts to the fishery by
comparing projected river dissolved oxygen values with tolerance levels for
various fish species. Zones of exclusion, linear distances, downstream
from dams from which fish would be excluded, will then be evaluated.
33
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3.0 RESULTS
3.1 WATER QUALITY
3.1.1 Hydropower Facility Development
The study area includes six locks and dams, two on the Allegheny
River, one on the Monongahela River, and three on the Ohio River. Hydro-
power conversion is being investigated at all of these locations.
Study Area Locks and Dams. The major design features of the study
area locks and dams (L/Ds) are identified in Table 3-1. Four have a fixed
crest design, therefore, no operating control on the overflow is possible.
These include the Allegheny L/D 2 and L/D 3, the Monongahela L/D 2, and the
Ohio River Dashields L/D.
The Ohio River Emsworth L/D includes a narrow uncontrolled spillway
(34.4 ft long at elevation 709.0) and a gated spillway (fixed sill eleva-
tion 698.0, 800 ft total length). There also is a back channel dam, with a
gated controlled spillway (600 ft total length with a fixed sill elevation
698.0). The Montgomery L/D includes an uncontrolled spillway (218 ft total
length with crest at 680.33) and a gated controlled spillway (1,000 ft
total length with a fixed sill elevation 667.0).
Hydropower Proposals. Hydropower projects are currently proposed for
the Dashields L/D, the Erasworth L/D, and the Montgomery L/D. The develop-
ment of hydropower projects at the other study area dams is in the planning
stage.
The Dashields L/D hydropower project is being applied for by Allegheny
County, Pennsylvania (C.E. Maguire 1983). The project includes a submerged
powerhouse and five bulb-type 5 MW horizontal turbine-generator units and
will replace about 250 ft of the present dam and spillway. The roof of the
powerhouse will be at the existing spillway elevation so that spillway
length and discharge capacity will not be reduced to any appreciable
34
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Table 3-1. Characteristics of study area lock and dams.
Allegheny River L/D 2
Location - Allegheny River Mile 6.7
Type - Fixed crest, 1393.0 ft length, 721.0 elevation
Normal Pool Elevation - Upper 721.0, Lower 710.0
Allegheny River L/D 3
Location - Allegheny River Mile 14.5
Type - Fixed crest, 1435.75 ft length, 734.5 elevation
Normal Pool Elevation - Upper 734.5, Lower 710.0
Monongahela River L/D 2
Location - Monongahela River Mile 11.2
Type - Fixed crest, 747.92 ft length, 718.7 elevation
Normal Pool Elevation - Upper 718.7, Lower 710.0
Ohio River, Emsworth L/D
Location - Ohio River Mile 6.2
(back channel dam is at Mile 6.8)
Type - Controlled spillway, 8 gated sections at 100 ft each,
fixed sill elevation 698.0; uncontrolled spillway, fixed
weir adjacent to river wall, 34.42 ft length, crest
elevation 709.0
Back Channel Dara - controlled spillway, 6 gated sections
each at 100 ft length, fixed sill elevation 698.0
Normal Pool Elevation - Upper 710.0, Lower 692.0
Ohio River, Dashields L/D
Location - Ohio River Mile 13.3
Type - Fixed crest, 1585 ft length, 692.0 elevation
Normal .Pool Elevation - Upper 692.0, Lower 682.0
Ohio River, Montgomery L/D
Location - Ohio River Mile 31.7
Type - Controlled spillway, 10 gated sections at 100 ft each,
fixed sill elevation 667.0; uncontrolled spillway, 2 fixed
weir sections at 109 ft length each, crest elevation 680.33
Normal Pool Elevation - Upper 682.0, Lower 664.5
Source: U.S. Army Corps of Engineers 1984a, 1984b.
35
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extent. The structure will include inlet and tailrace channels for the
turbines. The flow range for one turbine operation is 1,500 cfs minimum to
6,700 cfs maximum, with maximum capacity at 33,500 cfs for all five units.
The power plant will not operate with a flow in the river less than 2,500
cfs or more than 80,000 cfs.
The Emsworth L/D hydropower project is being applied for by the
Allegheny Electric Cooperative, Inc. (C.T. Main 1984). The project
includes construction of an intake channel, powerhouse, and tailrace with
two 10 MW full-Kaplan bulb-type turbines. The construction will require
removal of 95 feet of the 101-foot long uncontrolled spillway. The struc-
ture will have a top-of-roof deck elevation of about 701.0 feet, which is
two feet above the 100-year flood elevation. The minimum flow required for
operation is 6,450 cfs, including 3,600 cfs for turbine flow, and 2,850 cfs
for leakage and uncontrolled spillway flow. Between river flows of 6,450
and 21,850 cfs, all flow will pass through the turbines (except the leakage
flow of 2,850 cfs).
The Montgomery L/D hydropower project is also owned by Allegheny
Electric Cooperative, Inc. The project would include a 20 MW hydroelectric
generating facility utilizing full-Kaplan bulb-type turbines (14,400 HP
each). Complete specifications are not currently available for the
proposed hydroelectric retrofit (C.T. Main 1984).
3.1.2 Results of Calibration and Verification
The selection of model parameters and the model set-up for these
analyses followed the methods described in Chapter 2. During calibration,
it was found that the hydraulic parameters could be adjusted to model
observed conditions in the rivers very well for the flow regimes under
evaluation. The oxidation rates for biochemical oxygen demand and for
ammonia oxidation were selected based on previous work by ORSANCO (ORSANCO
1974). The parameters for algal dynamics were selected based on a review
of available data. The reaeration rate for the rivers and for the locks
and dams were selected based on the evaluations discussed below.
36
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Reaeration. River reaeration includes oxygen transfer resulting from
turbulence and diffusion into the water column, and oxygen transfer from
the production of dissolved oxygen by algae. Reaeration at the locks and
dams is discussed in the next section.
A recent assessment of the literature identified more than 20 predic-
tive equations for river reaeration due to the physical (hydraulic) charac-
teristics of the river (WAPORA 1984b). The conditions upon which these
equations were developed indicated that the O'Connor-Dobbins predictive
equation should be a reasonable technique for estimating the reaeration
rate, K2> for the study area rivers. Therefore, the QUAL II model Option
3 (O'Connor-Dobbins equation) was used. This resulted in the model
calculating the reaeration rate, K£» for each reach. The rates
calculated for the calibration and verification runs are shown in Table
3-2. This represents the physical transfer of oxygen into the river.
Modeling of algal activity using QUAL II requires estimating various
rates and constants for the entire study area (invariant parameters) and
for each reach (reach variant parameters). The invariant model parameters
that could affect the oxygen levels in the stream include algal respiration
and photosynthesis rates. These parameter values were selected based on
the recommended values (Chapter 2). The sensitivity of the selected values
was tested under a wide range of conditions, as discussed in a later
section.
The reach variant parameters used in controlling the algal oxygen
contribution in the study area were the light extinction coefficient and
the algal settling rate. The light extinction coefficient was used to
control the algal growth, whereas algal settling rates were used to control
instream concentrations of chlorophyll a_ (e.g., settling increased to
reduce instream chlorophyll a^ levels), which resulted in the indrect
control of dissolved oxygen levels. During calibration these parameter
values were adjusted for each reach, within the accepted limits, In order
to match as closely as possible observed dissolved oxygen and chlorophyll a^
levels. The values for these parameters were developed during calibration
and were then used during verification.
37
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1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
Reaeration rates predicted by the model (O'Connor-Dobbins) for
verfication and calibration.
Reaeration Rate, K~,
Calibration (day-lj
0.295
0.295
0.295
0.295
0.295
0.295
0.295
0.269
0.269
0.269
0.269
0.269
0.091
0.092
0.092
0.120
0.120
0.120
0.120
0.120
0.120
0.120
0.123
0.123
0.094
0.094
0.094
Reaeration Rate, K?,
Verification (day-l)
0.168
0.168
0.168
0.168
0.168
0.168
0.168
0.337
0.337
0.337
0.337
0.337
0.088
0.089
0.089
0.116
0.116
0.116
0.116
0.117
0.117
0.120
0.120
0.120
0.091
0.091
0.091
38
-------
The data sets used for model calibration and verification indicated
that portions of each river were above saturation dissolved oxygen levels.
This was interpreted to mean that algal activity in the study area is a
significant source of dissolved oxygen (see Greeson 1967). Based on this,
the algal growth parameters were adjusted to approximate the level of algal
activity (represented as chlorophyll a) without attempting to exactly match
the observed concentrations. The sensitivity of the dissolved oxygen
predictions to the selected values for these parameters was evaluated
during the modeling to determine the reasonableness of this approach. As
described in a later section, the sensitivity analyses confirmed the
general reasonableness of the values selected.
Lock and Dam Reaeration. The flow across a dam can be a significant
source of reaeration and is a major concern in this study. It is generally
considered that the reaeration across a dam is a function of the head loss,
the dissolved oxygen deficit, water conditions (temperature and contamina-
tion), and the physical characteristics of the dam. The dam reaeration
formula used in the QUAL II model is the equation (WAPORA 1984a):
1 n
Da-Dd - 1 a
1 + 0.11 a b H (1 + 0.046 T)
where:
Da = dissolved oxygen deficit above dam, mg/1
Djj = dissolved oxygen deficit below dam, mg/1
a = coefficient characteristic of water quality
(1.8 = clean water; 1.6 a slight contamination;
1.0 = moderate contamination; 0.65 = gross
contamination)
b = dam characteristic
H =» height through which water falls, feet
T = temperature, °C
The water in the study area rivers was considered to be slightly
contaminated (a =¦ 1.6). As summarized in Table 3-3, the value for b for
each dam was developed from dissolved oxygen data provided by the Corps of
39
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Table 3-3. Summary of dam characteristic values computed for the study area
dams.
Survey
D
D
Identification
Date
T,°C
mg/i
mg/1
b
Monongahela L/D
2
7/31/75
29.9
1.61
1.34
0.055
height = 8.7 ft
6/23/78
26.2
1.14
0.81
0.121
6/28/79
26.2
0.81
0.73
0.032
7/24/80
24.3
1.35
0.85
0.181
8/26/83
28.6
1.50
1.28
0.048
0.10
Allegheny L/D 2
8/26/76
25.2
0.0
-0.14
—
height = 11.0
ft
6/30/77
25.3
0.18
-0.28
—
7/20/77
26.7
1.20
-0.11
—
8/10/78
24.0
1.05
0.21
0.989
7/13/79
16.1
2.13
0.99
0.344
7/23/81
25.2
1.05
-0.02
—
7/19/82
28.0
0.57
-0.18
—
7/22/82
28.0
0.80
0.20
0.682
7/28/83
28.0
0.15
-0.06
—
0.67
Allegheny L/D 3
8/26/76
25.2
0.59
0.04
2.684
height = 13.5
ft
6/30/77
27.2
0.50
-0.74
—
7/20/77
26.4
0.85
0.79
0.015
8/10/78
24.4
1.42
0.61
0.263
7/12/79
23.9
0.58
-0.19
—
7/23/81
25.4
1.52
0.70
0.227
7/19/82
28.0
1.18
0.41
0.345
7/22/82
28.0
1.16
0.70
0.121
7/28/83
27.9
0.92
0.17
0.811
0.64
Emsworth L/D
9/22/75
18.0
0.44
0.25
0.133
height = 18.0
ft
6/06/77
23.7
1.81
1.24
0.070
7/24/78
26.8
1.26
0.54
0.191
8/13/79
24.7
0.84
0.80
0.007
8/02/82
25.4
1.32
1.45
—
7/11/83
24.3
0.63
0.19
0.351
8/01/83
27.7
1.06
0.14
0.924
0.28
Dashields L/D
9/22/75
18.0
0.39
-0.19
—
height = 10.0
ft
6/06/77
23.4
1.72
0.40
0.906
7/24/78
26.6
0.92
-0.25
—
8/13/79
24.8
1.06
0.74
0.114
8/02/82
25.4
1.45
0.99
0.121
7/11/83
25.0
0.82
0.26
0.570
8/01/83
27.6
0.63
-0.62
—
0.43
sdn_j[ * 0.06a
sc*n-i
= 0.32
sdn_j = 0.94
sdn_2 = 0.34
sdn_i = 0.38
40
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Table 3-3. (continued)
Survey
D
D
Identification
Date
TOC
rag/1
m^/l
b
Montgomery Island L/D
9/23/75
17.9
0.41
-0.76
T--
height = 17.5 ft
6/07/77
23.0
2.43
-0.03
7/25/78
27.0
0.68
0.06
1.470
8/14/79
24.2
0.94
-0.34
—
8/13/82
26.2
2.68
0.65
0.453
7/12/83
24.8
0.75
0.00
—
8/02/83
27.2
0.86
-0.49
—
0.96 sd^ - 0.72
asdn_i represents the unbiased standard deviation of the values for b
41
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Engineers. The observed reaeration at each dam (indicated by upstream and
downstream dissolved oxygen measurements in the rivers) was used to calcu-
late b. The dam height (H) was estimated as the difference between the
upper and lower pool elevations. The modeling was performed using the b
for each lock and dam (Table 3-3) and the H based on pool elevations.
Calibration Results. The predicted average dissolved oxygen levels
for the Ohio River, the Allegheny River, and Monongahela River are pre-
sented in Figures 3-1 through 3-3. The observed dissolved oxygen levels
for the calibration data set are also presented in these figures with the
upper and lower reported values shown. Concurrence between the predicted
and observed dissolved oxygen levels is considered good. The areas where
the predicted dissolved oxygen deviates most from the observed levels
correspond to locations where the river levels are greater than saturation.
The rivers/temperatures were about 28°C, indicating a saturation dissolved
oxygen level of about 7.9 mg/1.
It is possible for the QUAL II model to predict dissolved oxygen
levels above saturation when the contribution from algal photosynthesis is
sufficiently large. The adjustments to the algal growth parameters made
during calibration reflect this, with dissolved oxygen levels predicted
above saturation at several locations. These adjustments were constrained
to generally agree with reported levels of chlorophyll in the data set.
As a result, it was not possible to exactly match the data set.
Another characteristic of the data set could not be matched. The
dissolved oxygen data indicated an increase downstream of the Montgomery
L/D even though the upstream levels were greater than saturation. The
predictive equation used by the model for dam reaeration would result in a
decrease in dissolved oxygen in this situation. Therefore, it was impossi-
ble to exactly match the observed conditions during calibration.
Verification Results. The calibrated model was tested using a second
data set for the Ohio River and the two tributaries. The adjustments to
the model for these runs included only modification of headwater and point
source conditions. All other parameters, including the reaeration predic-
42
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-
O 6.0
:il
28 28 24 22 20 18 16 14 12
OHIO RIVER MILES (From Three Rivers)
Figure 3-1. Dissolved oxygen predictions and observed data for QUAL II model cali-
bration of the Ohio River (data set 11 July 1983).
-------
o 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15
MONONGAHELA RIVER MILES
Figure 3-2. Dissolved oxygen predictions and observed data for QUAL II model cali-
bration of the Monongahela River (data set 26 August 1983).
-------
o 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15
ALLEGHENY RIVER MILES
Figure 3-3. Dissolved oxygen predictions and observed data for QUAL II model cali-
bration of the Allegheny River (data set 28 July 1983).
-------
tive method and dam characteristics, were retained at the values developed
during model calibration. However, the reaeration predictive method
(O'Connor-Dobbins) relies on stream velocity to develop K2* Stream
velocity is computed by the QUAL II model based upon stream flow. Since
flows for the verification and calibration data sets differed, different
reaeration rates for the two flow regimes were used (see Table 3-2).
Figures 3-4, 3-5, and 3-6 present the verification data and model
predictions for the Ohio mainstem and the two tributaries. The predicted
dissolved oxygen levels are greater than saturation at some locations. The
river temperatures were about 24.5 to 25.0°C, indicating a saturation
dissolved oxygen level of about 8.4 mg/1. Also, the chlorophyll ji predic-
tions were consistent with the observed conditions of about 10 yg/1. These
predictions are considered good, and indicate that the calibrated model is
a reasonably accurate predictive tool for dissolved oxygen.
Sensitivity Analyses. During calibration, the model was run with a
wide range of parameter values to determine the sensitivity of the
dissolved oxygen predictions. The parameters evaluated included the
carbonaceous and nitrogenous oxidation rates; the reaeration (K2) predic-
tion method; and algal parameters, photosynthesis and respiration rates,
light extinction coefficient, and algal settling rate. The range evaluated
was typically an order of magnitude per parameter, unless physical
constraints or river conditions indicated that a smaller range was more
appropriate. As described in Chapter 2, there are many other parameters
that could be adjusted, but those selected were considered to be most
critical for the study area.
Oxidation Rates. The oxidation rates for the carbonaceous and
nitrogenous reactions can directly affect dissolved oxygen predictions
because these represent major oxygen sinks. In particular, the nitrogenous
oxygen demand had been identified by previous modeling to be a significant
sink for the study area (ORSANCO 1974).
The carbonaceous oxidation rate was varied from 0.1 to 0.01
day-*, and the value of 0.01 day-* was selected for modeling. It
46
-------
I-Ul i
I
28 28 24 22 20 18 18 . 14 12
OHIO RIVER MILES (From Three Rivers)
Figure 3-4. Dissolved oxygen predictions and observed data for QUAL II model veri-
fication of the Ohio River (data set 1 August 1983).
-------
in^nui:
:i;
|Tt
r rm
~; :fii
in'm '
l-'-'-ip-J'v
5 6 7 8 9 10
MONONGAHELA RIVER MILES
Figure 3-5. Dissolved oxygen predictions and observed data for QUAL II model veri-
fication of the Monongahela River (data set 24 July 1980)•
-------
1
minium ii
iiiiuiiiiiiiii
5 6 7 8 9 10
ALLEGHENY RIVER MILES
11 12
14 15
Figure 3-6. Dissolved oxygen predictions and observed data for QUAL II model veri-
fication of the Allegheny River (data set 23 July 1981).
-------
was found that dissolved oxygen values were insensitive to carbonaceous
oxidation rates (less than 0.1 mg/1 change in DO predicted).
The nitrogenous rate was varied from 0.10 to 0.01 day-*, and the
value of 0.1 day-* was selected for modeling. It was found that the
dissolved oxygen was more sensitive to this rate than to the carbonaceious
oxidation rate. A maximum change of 0.3 mg/1 was observed at the highest
rate versus the lowest rate.
It was concluded from this analysis that the rates selected were
adequate for further use in the modeling. The predicted dissolved oxygen
levels should not be particularly sensitive to slight changes in values for
these parameters.
Reaeration Rates. The sensitivity of the model calibration to the
method selected for predicting reaeration was evaluated by running the
other options available in the QUAL II model (WAPORA 1984a). It was found
that many of the other predictive equations generated reaeration rates
generally similar to the O'Connor-Dobbins method and yielded similar
dissolved oxygen predictions. A rigorous analysis was not performed to
identify the relative accuracy of these predictions, but inspection of the
results indicated that the O'Connor-Dobbins method provided the best
match.
Another sensitivity analysis conducted involved selecting reaeration
rates (K2) from 0.1 to 1.0 day-*. This was performed while also
adjusting the flow through the hydropower turbines at 0 percent (i.e.,
existing conditions) and 100 percent (i.e., maximum hydropower develop-
ment). The impact on dissolved oxygen predictions for existing conditions
(0 percent hydropower) while increasing K2 from 0.1 to 1.0 day-* was
an increase in the predicted dissolved oxygen at the higher rate that
ranged from 0.6 to 1.7 mg/1 greater than at the lower rate for the study
area reaches. When maximum hydropower development (100 percent flow
through the turbines and no reaeration from the dams) was modeled, the
predicted dissolved oxygen at the higher rate (1.0 day-*) was 1.0 to
4.5 mg/1 higher than at the lower rate (0.1 day-*).
50
-------
These results indicate that the selection of the reaeration rate (or
method) is a major potential source of error in the accuracy of the
dissolved oxygen predictions during calibration. However, the accuracy of
the selected method during calibration and verification indicates that the
potential error in this study is probably not very large.
Algal Parameters. The algal parameters were varied while the reaera-
tion option was kept constant (i.e., the O'Connor-Dobbins equation). The
algal parameter values were selected to maintain chlorophyll ja predictions
near the observed levels. The impact on dissolved oxygen was used as the
indicator of model sensitivity.
The invariant model parameters adjusted during the sensitivity
analyses included oxygen production by algae (photosynthesis) and oxygen
uptake by algae (respiration). The initial model runs were made using
values consistent with the available literature: oxygen production = 1.8
mgO/mgA; oxygen uptake = 2.3 mgO/mgA. During sensitivity analyses, the
oxygen production was Increased to 2.0 mgO/mgA and oxygen uptake was
decreased to 1.4 mgO/mgA. These changes produced results that better
matched the observed conditions. However, the changes resulted in an
increase in predicted dissolved oxygen levels of about 0.3 mg/1, when
compared to the initial values.
The light extinction coefficient was lowered from an initial value of
2.0 ft~* to an extreme value of 0.2 ft-*. This resulted in
increased algal production, with a higher chlorophyll a^ concentration and
an increased instream dissolved oxygen level. The chlorophyll concentra-
tion was used to control the adjustments to the algal settling rate. The
order of magnitude decrease (2.0 to 0.2 ft-*) predicted a dissolved
oxygen increase of about 0.5 mg/1. The light extinction coefficient values
selected for the calibrated model were fairly accurate in predicting
dissolved oxygen and chlorophyll a_ values. The accuracy of the selected
values also was indicated by predicted Secchi disc readings of 2 to 3 ft,
which are consistent with the observed conditions for the calibration and
verification data sets.
51
-------
The algal settling rate was increased from 4.0 to 6.0 ft-*, with a
resulting decrease in dissolved oxygen of about 0.2 mg/1. This indicates a
low sensitivity of dissolved oxygen to this parameter. The algal settling
rate as used in the QUAL II model represents a removal mechanism for algae
(chlorophyll a). The adjustment from 4.0 to 6.0 ft-^ resulted in a
decrease in chlorophyll a^ of about 3 yg/1.
The results of the model sensitivity runs indicated that the dissolved
oxygen levels predicted by QUAL II are most sensitive to the light extinc-
tion coefficient. This agrees with observations by others (Miller personal
communication). It has been hypothesized that algal blooms observed in the
Ohio River are triggered by low velocities at the lower stream flow rates.
This results in reduced turbidity and greater light penetration (Miller
personal communication).
Evaluation of Calibrated Model Performance. The ability of the model
to accurately predict dissolved oxygen conditions in the study area rivers
was analyzed by comparing the observed conditions in each data set to the
predictions during calibration and verification. This evaluation is
summarized in Table 3-4. These results indicate that the model performed
well during both calibration and verification.
3.1.3 Projected Water Quality With Hydropower Development
The calibrated and verified QUAL II water quality model was used to
predict the effect of hydropower development on study area river dissolved
oxygen levels. Hydropower development was simulated by varying the amount
of flow passing over the dam versus passing through a turbine. The levels
of water quality parameters other than dissolved oxygen also were predicted
by the model. These predictions are not discussed in this report, since
dissolved oxygen was the focus of the present study. Moreover, it was
observed that the flow adjustments for dam reaeration did not have an
affect on the predicted levels of the other parameters.
Conditions Evaluated. Low flow and hot summer weather were the
critical conditions selected for modeling. These summer conditions were
52
-------
Table 3-4. Performance statistics for calibration and verification of QUAL
II model (dissolved oxygen data).
Calibration Data
Ohio River
Allegheny River
Monongahela River
Average
Error
mg/1
0.38
0.15
0
Absolute
Value
Error
rcg/1
0.38
0.15
0
RMS
Error
mg/1
0.56
0.21
0
Average
Percent
Error
4.7
1.9
0
Verification Data
Ohio River 0.13
Allegheny River 0.19
Monongahela River -0.08
0.13
0.20
0.08
0.25
0.30
0.16
2.2
2.7
1.45
where:
Average Error
n
I 0-P
Absolute Value Error = - E /O-P/
RMS Error = E (0-P)2j1/2
Average Percent Error = ^
0 = observed data
P = model predicted data
53
-------
selected based on a review of ambient conditions observed in the study area
between 1978 and 1983. Worst case conditions reported for August 1983
(Ohio River temperature 26.7°C) was selected. The most important aspect of
selecting this temperature is to establish the level of dissolved oxygen
saturation. Higher temperatures lower the dissolved oxygen saturation
level, while lower temperatures increase the saturation level. Sensitivity
analyses for the affect of temperature selection were not performed for
this study using the water quality model.
The flow conditions selected for the modeling analysis included the
lowest Long Terra Monthly Average (LTMA) and the Lowest Flow Expected (LFE).
These flows were estimated for the headwaters (Allegheny at Mile 15.0 and
Monongahela at Mile 15.0) and a tributary (Beaver River). Flows at other
points in the study area were determined for the modeling using point
source flows and a mass balance. The available flow data included gage
information at the Allegheny River (Mile 13.3), Monongahela River (Mile
11.2), Ohio River (Mile 15.2), and the Beaver River (Mile 5.3). These data
were combined using a flow balance to develop the flow rates in the model,
as presented in Table 3-5.
The impacts of hydropower development were evaluated by considering a
fraction of the available flow for passage through the turbines as opposed
to across the dam. The flow through the turbine was modeled at 0 percent,
50 percent, and 100 percent of the river flow. The condition with zero
flow through the turbine was modeled to establish the baseline condition.
The 50 percent and 100 percent flow conditions were run at all locks and
dams to reflect a varying level of conversion to hydropower. The cumula-
tive impact of hydropower development at all locks and dams is indicated by
the successive changes in dissolved oxygen levels (as predicted by the
model) as a function of increasing distance down river. The impact at a
specific lock and dam can be inferred by the shape of the dissolved oxygen
curve upstream and downstream of the facility.
Model Predictions. The impact of hydropower conversion on dissolved
oxygen is presented for the three rivers in Figures 3-7, 3-8, and 3-9, for
the lowest LTMA flow rate. The baseline condition on the rivers (0 percent
54
-------
Table 3-5. Flow rates used in impact analysis.
Long Term Monthly Average (LTMA) (lowest value)
Location
HW Allegheny (15.0)
HW Monongahela (15.0)
Ohio River (0.0)
Beaver River (enters
Ohio River at 25.6)
Ohio River (25.6)
Flow
(cfs)
4,730
3,990
8,720
1,410
10,430
Basis
Records at Mile 13.3, for September flow
average (0RSANC0 1984)
Calculated from flow balance with
Allegheny and Ohio Rivers, and intermed-
iate point source flows
Records at Mile 15.2, for September flow
average (9,020 cfs) adjusted for inter-
mediate point source flows
Records at Mile 5.3 on Beaver River, for
September flow average
Calculated from flow balance
Lowest Flow Expected (LFE)
Location
HW Allegheny (15.0)
Flow
(cfs)
1,890
HW Monongahela (15.0) 1,440
Ohio River (0.0) 3,330
Beaver Run (enters 670
Ohio River at 25.6)
Basis
Calculated from flow balance with
Monongahela and Ohio Rivers
Records at Mile 11.2, for lowest flow
observed September 1983
Records at Mile 15.2, for lowest flow
observed September 1983 (3,630 cfs),
adjusted for intermediate point source
flows
Records at Mile 5.3 on Beaver River, for
lowest flow observed September 1983
Ohio River (25.6)
4,300
Calculated from flow balance
55
-------
OHIO RIVER MILES (From Three Rivers)
Figure 3-7. Model prediction for Long Term Monthly Average (LTMA) flow for the
Ohio River. Three scenarios for Hydropower Retrofit (1.0 = ambient
conditions; 0.5 = partial hydropower development; 0.0 = development
at all dams) .
-------
0 1 2 3 4 5 6 7 8 9 10 11 12 13 14 15
MONONGAHELA RIVER MILES
Figure 3-8. Model prediction for Long Term Monthly Average (LTMA) flow for the
Monongahela River. Three scenarios for Hydropower Retrofit (1.0 =
ambient conditions;- 0.5 = partial hydropower development; 0.0 °
development at all dams).
-------
tn
oo
^ 7.0
O
2
111
O
>-
X
O
Q
UJ
>
_l
O
in
w
Q
I
T-*r
H-SHrr
4.0
3.0
5 6 7 8 9 10
ALLEGHENY RIVER MILES
Figure 3-9. Model prediction for Long Term Monthly Average (LTMA) flow for the
Allegheny River. Three scenarios for Ilydropower Retrofit (1.0 =
ambient conditions; 0.5 = partial hydropower development; 0.0 ¦=
development at all dams).
-------
hydropower development) reflects the maximum reaeration condition; with
hydropower development there is a decrease in reaeration. The reaeration
predicted in this analysis for the locks and dams was:
Source
DO Increase at
0% Hydropower
mg/1
DO Increase at
50% Hydropower
mg/1
DO Increase at
100% Hydropower
mg/1
LTMA
LFE
LTMA
LFE
LTMA LFE
Allegheny L/D 2
0.2
0
0.15
0
0 0
Allegheny L/D 3
0.6
0.6
0.3
0.2
0 0
Monongahela L/D 2
0.25
0.2
0.12
0.1
0 0
Ohio Emsworth L/D
0.7
1.0
0.4
0.5
0 0
Ohio Dashields L/D
0.4
0.5
0.3
0.4
0 0
Ohio Montgomery L/D
0.6
0.8
0.4
0.5
0 0
A cumulative impact from hydropower development would be demonstrated
as a dissolved oxygen deficit that increases down river at higher levels of
hydropower conversion. At Ohio River Mile 40.0, the difference between the
existing condition (0 percent hydropower) and the maximum hydropower
conversion dissolved oxygen levels is 1.4 mg/1, while the difference at
Ohio River Mile 0.0 is 0.4 mg/1. The existing condition dissolved oxygen
is predicted to remain at high levels, while the maximum hydropower
development shows a slightly degraded condition. This indicates that the
loss of reaeration by reducing flow over the locks and dams will be
demonstrated as a cumulative impact. However, the loss in reaeration will
be partially offset by higher reaeration in the river due to the higher
deficit in the river. The results for the LTMA condition, as shown in
Figure 3-7, do not indicate that the cumulative impact would cause a water
quality violation (i.e., dissolved oxygen below 5.0 mg/1). The results in
Figures 3-8 and 3-9 do not demonstrate a significant impact.
The impact of hydropower conversion on dissolved oxygen for the Lowest
Flow Expected (LFE) is presented in Figures 3-10, 3-11, and 3-12. These
results generally agree with the results from the LTMA evaluation.
However, the dissolved oxygen levels show a more rapid decrease downstream
of the Montgomery L/D. The results do not indicate a water quality viola-
tion within the study area, but extending the curves (at the same rate of
decline) would result in a dissolved oxygen of 5.0 mg/1 at about River Mile
51 for the 100 percent flow conditions. This could indicate the potential
for adverse impacts downstream of the study area.
59
-------
9.0
n::irn:j:r..
¦k-w
iiiiiiiiiiiiiiiiiiiutYfium
•laiiiiiiiMiiiiitiiitnntvt
26 26 24 22 20 18 16 14 12
OHIO RIVER MILES (From Three Rivers)
Figure 3-10. Model prediction for Low Flow Expected (LFE) flow for the Ohio River.
Three scenarios for Hydropower Retrofit (1.0 = ambient conditions;
0.5 = partial hydropower development; 0.0 = development at all dams).
-------
ijjHnSSgSgsssi
0 1 2 3 4 5 6 7 8 9 • 10 1 1 12 13 14 15
MONONQAHELA RIVER MILES
Figure 3-11. Model prediction for Low Flow Expected (LFE) flow for the Monongahela
River. Three scenarios for Hydropower Retrofit (1.0 =» ambient condi-
tions; 0.5 = partial hydropower development; 0.0 = development at all
dams).
-------
cn
ro
O
2
2
111
O
>-
x
O
a
LU
>
_l
o
w
w
lliSli!
iiEI
*+*f
:i;i (i:
SEP
: ¦ '¦]-1
Ij'f ,
: -II'!
!:
5 6 7 8 9 10
ALLEGHENY RIVER MILES
Figure 3-12. Model prediction for Low Flow Expected (LFE) flow for the Alle-
gheny River. Three scenarios for Hydropower Retrofit (1.0 =
ambient conditions; 0.5 = partial hydropower development; 0.0 =
development at all dams).
-------
3.2 THE STUDY AREA FISHERY
3.2.1 Composition of the Community
A thorough historical perspective regarding ichthyological studies of
the Ohio River basin, documentation of changes in composition of the
fishery along the river and through time, and attendant changes resulting
from man's activities has been prepared by Lachner (1956), ORSANCO (1962),
Krumholz (1981), Trautman (1981), and Pearson and Kruraholz (1984). These
sources document changes in the fishery from the period of colonization of
the basin by Europeans to the 1980's. They ascribe major changes in the
fishery to increases in turbidity and siltation as a result of clearing of
the watershed for farming; depression of dissolved oxygen concentrations as
a result of population increases in metropolitan areas and increased
discharge of septage to study area rivers; degradation of water quality as
a result of metal and organics discharges by industry; reduction of river
water pH as a result of acid mine drainage from the coal fields along the
Allegheny and Monongahela Rivers; and changes resulting from impounding the
free-flowing rivers to enhance navigation. Recent recovery of the fishery
of the upper basin has occurred as a result of the installation, use, and
upgrading of industrial and sanitary waste treatment facilities.
Some of the earliest accounts of the fishes of the Ohio River were
published by travelers on the Ohio prior to 1818 (Pearson and Krumholz
1984). Subsequently, regional, state, or Ohio River basin-wide fisheries
surveys have been conducted and have documented the occurrence of some 154
species. Through time, 111 species were reported from the river prior to
1920; between 1920 and 1969, 121 species were reported; and between 1970
and 1983, 130 species were collected. The upper basin, from Pittsburgh
downstream to River Mile 327, has yielded 120 species (Pearson and Krumholz
1984).
The study area, the upper Ohio River and lower reaches of the
Allegheny and Monongahela Rivers, has yielded 122 species (Table 3-6)
distributed among the following 20 families: Petromyzontidae (lampreys),
Acipenseridae (sturgeons), Polyodontidae (paddlefishes), Lepisosteidae
63
-------
Table 3-6. Fishes occurring in the upper mainstem of the Ohio River and
lower Allegheny and Monongahela Rivers.a»^
Family Name
Scientific Name
Common Name
Petromyzontidae
Ichthyomyzon bdellium
Ohio lamprey
Ichthyomyzon castaneus
Chestnut lamprey
Ichthyomyzon greeleyi
Allegheny brook lamprey
Ichthyomyzon unicuspis
Silver lamprey
Lampetra aepyptera
Least brook lamprey
Acipenseridae
Acipenser fulvescens
Lake sturgeon
Scaphirhynchus platorynchus
Shovelnose sturgeon
Polyodontidae
Polyodon spathula
Paddlefish
Lepisosteidae
Lepisosteus osseus
Longnose gar
Lepisosteus platostomus
Shortnose gar
Amiidae
Aroia calva
Bowfin
Family Name
Scientific Name
Common Name
Anguillidae
Anguilla rostrata
American eel
Clupeidae
Alosa chrysochloris
Skipjack herring
Alosa pseudoharengus
Alewife
Dorosoma cepedianum
Gizzard shad
Hiodontidae
Hiodon alosoides
Goldeye
Hiodon tergisus
Mooneye
Salmonidae
Salmo gairdneri
Rainbow trout
Salmo trutta
Brown trout
Esocidae
Esox americanus americanus
Redfin pickerel
Esox americanus verraiculatus
Grass pickerel
Esox lucius
Northern pike
Esox masquinongy
Muskellunge
64
-------
Table 3-6. (continued)
Family Name
Scientific Name
Common Name
Cyprinidae
Campostoma anomalum
Stoneroller
Carassius auratus
Goldfish
Clinostomus elongatus
Redside dace
Cyprinus carpio
Carp
Ericymba buccata
Silverjaw minnow
Hybopsis aestivalis
Speckled chub
Hybopsis amblops
Bigeye chub
Hybopsis dissimilis
Streamline chub
Hybopsis storeriana
Silver chub
Hybopsis x-punctata
Gravel chub
Nocomis micropogon
River chub
Notemigonus crysoleucas
Golden shiner
Notropis ariommus
Popeye shiner
Notropis atherinoides
Emerald shiner
Notropis blennius
River shiner
Family Name
Scientific Name
Common Name
Cyprinidae (continued)
Notropis boops
Bigeye shiner
Notropis buchanani
Ghost shiner
Notropis chrysocephalus
Striped shiner
Notropis comutus
Common shiner
Notropis heterolepis
Blacknose shiner
Notropis hudsonius
Spottail shiner
Notropis photogenis
Silver shiner
Notropis rubellus
Rosyface shiner
Notropis spilopterus
Spotfin shiner
Notropis stramineus
Sand shiner
Notropis umbratilis
Redfin shiner
Notropis volucellus
Mimic shiner
Notropis whipplei
Steelcolor shiner
Phenacobius mirabilis
Suckermouth minnow
Phoxinus erythrogaster
Southern redbelly dace
65
-------
Table 3-6. (continued)
Family Name
Scientific Name
Common Name
Cyprinidae (continued)
Pimephales notatus
Bluntnose minnow
Pimephales promelas
Fathead minnow
Pimephales vigilax
Bullhead minnow
Rhinichthys atratulus
Blacknose dace
Semotilus atromaculatus
Creek chub
Catostomidae
Carpiodes carpio
River carpsucker
Carpiodes cyprinus
Quillback
Carpiodes velifer
Highfin carpsucker
Catostomus commersoni
White sucker
Cycleptus elongatus
Blue sucker
Hypentelium nigricans
Northern hog sucker
Ictiobus bubalus
Smallmouth buffalo
Ictiobus cyprinellus
Bigmouth buffalo
Ictiobus niger
Black buffalo
Family Name
Scientific Name
Common Name
Catostomidae (continued)
Minytrema melanops
Spotted sucker
Moxostoma anisurum
Silver redhorse
Moxostoma carinatum
River redhorse
Moxostoma duquesnei
Black redhorse
Moxostoma erythrurum
Golden redhorse
Moxostoma macrolepidotum
Shorthead redhorse
Ictaluridae
Ictalurus catus
White catfish
Ictalurus furcatus
Blue catfish
Ictalurus melas
Black bullhead
Ictalurus natalis
Yellow bullhead
Ictalurus nebulosus
Brown bullhead
Ictalurus punctatus
Channel catfish
Noturus eleutherus
Mountain madtom
Noturus flavus
Stonecat
66
-------
Table 3-6. (continued)
Family Name
Scientific Name
Common Name
Ictaluridae (continued)
Noturus gyrinus
Tadpole madtom
Noturus miurus
Brindled madtom
Noturus stigmosus
Northern madtom
Pylodictis olivaris
Flathead catfish
Percopsidae
Percopsis omiscomaycus
Trout-perch
Cyprinodontidae
Fundulus diaphanus
Banded killifish
Fundulus notatus
Blackstripe topminnow
Atherinidae
Labidesthes sicculus
Brook silverside
Percichthyidae
Mo rone chrysops
White bass
Morone saxatilis
Striped bass
Centrarchidae
Ambloplites rupestris
Rock bass
Family Name
Scientific Name
Common Name
Centrarchidae (continued)
Lepomis cyanellus
Green sunfish
Lepomis gibbosus
Pumpkinseed
Lepomis gulosus
Warmouth
Lepomis humilis
Orangespotted sunfish
Lepomis macrochirus
Bluegill
Lepomis megalotis
Longear sunfish
Lepomis microlophus
Redear sunfish
Micropterus dolomleui
Smallmouth bass
Micropterus punctulatus
Spotted bass
Micropterus salmoides
Largemouth bass
Pomoxis annularis
White crappie
Pomoxis nigromaculatus
Black crappie
Percidae
Ammocrypta pelluclda
Eastern sand darter
67
-------
Table 3-6. (continued)
Family Name
Scientific Name
Common Name
Family Name
Scientific Name
Common Name
Percidae (continued)
Percidae (continued)
Etheostoma blennioides
Greenside darter
Percina copelandi
Channel darter
Etheostoma caeruleum
Rainbow darter
Percina macrocephala
Longhead darter
Etheostoma flabellare
Fantail darter
Percina maculata
Blackside darter
Etheostoma nigrum
Johnny darter
Percina oxyrhyncha
Sharpnose darter
Etheostoma spectabile
Orangethroat darter
Stizostedion canadense
Sauger
Etheostoma variatum
Variegate darter
Stizostedion vitreum vitreum
Walleye
Etheostoma zonale
Banded darter
Perca flavescens
Yellow perch
Percina caprodes
Logperch
Sciaenidae
Aplodinotus grunniens
Freshwater drum
Cottidae
Cottus bairdi
Mottled sculpin
Nomenclature used herein follows that of Bailey, et al. 1970.
^Sources Reviewed: ORSANCO 1977, 1981; Pearson and Krumholz 1984; Energy
Impact Assoc. 1978, 1980; Raney 1938; Geo-Marine, Inc.
1978, 1981, 1982; WAPORA, Inc. 1973, 1974, 1975, 1976,
1977, 1978, 1979, 1980, 1981; Trautraan 1981; NUS 1975,
1979a and b, 1982; Atlantic Power Development Corp.
1983; Allegheny County, PA 1982; Allegheny Electric
Cooperative, Inc. 1982; C.E. Maguire 1983a and b; Chas.
T. Main, Inc. 1984; Burgess & Niple, Ltd. 1983;
Allegheny Power System 1977; Krumholz 1981; Pennsyl-
vania 'Power Company 1976; Westinghouse Electric Corp.
1975a, b, c, d, e, and f, 1976, 1977; Denoncourt, et
al. 1975; Preston and White 1978; Smith and Shema 1982;
U.S. Army Corps of Engineers 1978, 1980; Ecological
Analysts, Inc. 1978, 1979; Preston 1974; Equitable
Environmental Health, Inc. 1979a and b; Duquesne Light
Co. 1977, 1979; Krumholz and Minckley 1964.
68
-------
(gars), Amiidae (bowfins), Anguillidae (eels), Clupeidae (herrings),
Hiodontidae (mooneyes), Salmonidae (trouts), Esocidae (pikes), Cyprinidae
(minnows and carps), Catostornidae (suckers), Ictaluridae (freshwater cat-
fishes), Percopsidae (trout-perches), Cyprinodontidae (killifishes),
Atherinidae (silversides), Percichthyidae (temperate basses), Centrarchidae
(sunfishes), Percidae (perches), Sciaenidae (drums), and Cottidae (scul-
pins). Species introduced to the river or within the Ohio River basin
include the alewife (Alosa pseudoharengus), rainbow trout (Salmo gaird-
neri), brown trout (S^. trutta), northern pike (Esox lucius), goldfish
(Carassius auratus), common carp (Cyprinus carpio), white catfish
(Ictalurus catus), banded killifish (Fundulus diaphanus), and striped bass
(Morone saxatllis) (Trautman 1981, Pearson and Krumholz 1984). Lachner
(1956) noted that there has been considerable change in the fish fauna of
the upper Ohio River basin since the early nineteenth century. The
following species, some of which were common or abundant before 1900,
currently have greatly reduced populations or have been extirpated from the
upper basin: paddlefish (Polyodon spathula), lake sturgeon (Acipenser
fulvescens), shortnose gar (Lepisosteus platostomus), bowfin (Amia calva),
goldeye (Hiodon alosoides), gizzard shad (Dorosoma cepedianum), smallmouth
buffalo (Ictiobus bubalus), highfin carpsucker (Carpiodes velifer), river
carpsucker (C. carpio), blue sucker (Cycleptus elongatus), river shiner
(Notropis blennius), blue catfish (Ictalurus furcatus), sauger
(Stizostedion canadense), and freshwater drum (Aplodinotus grunniens). The
Ohio lamprey (Ichthyomyzon bdellium), shorthead redhorse (Moxostoma
breviceps), spotted sucker (Minytrema melanops), flathead catfish
(Pylodictis olivaris), and warmouth (Lepomis gulosus) are only rarely
captured from the upper Ohio River basin.
3.2.2 Relative Abundance of Fishes in the Allegheny, Monongahela, and Ohio
Rivers
Characterization of the relative abundance of fishes, diversity, and
changes in fish species composition through time for the Allegheny,
Monongahela, and Ohio Rivers for the period encompassing settlement through
the . mid-19501s are difficult to interpret due to a paucity of fisheries
surveys (Pearson and Krumholz 1984). However, in 1957, the "Aquatic-Life
Resources Project" was initiated, and sampling was conducted through 1959.
69
-------
The objective of this study was to appraise the suitability of the Ohio
River for maintenance of aquatic life, with emphasis centering on determi-
nation of the species composition, the distribution, and the relative
abundance of fishes of the lower reaches of the Allegheny and Monongahela
Rivers, and the entire length of the Ohio River. During this project, fish
were sampled by electrofishing; seining; trawling; netting with hoop nets,
trammel nets, and gill nets; and by rotenoning Ohio River and tributary
lock and dam-lock chambers, stream mouths, backwaters, and other shoreline
areas. The results of these surveys were published in 1962 (ORSANCO 1962).
Lock chamber fish surveys were again undertaken in 1967, and samples have
been collected from various locations along study area rivers from 1967 to
date (ORSANCO 1981, ORSANCO personal communication). The results of the
1967 through 1980 lock chamber studies for the main stem of the Ohio River
were compiled and summarized by Pearson and Krumholz (1984). Results of
lock chamber rotenone studies for the Allegheny and Monongahela Rivers were
compiled by ORSANCO (1981). The lock chamber rotenone studies are one
source of fisheries information that has been gathered continuously for
over 25 years and will be used here to document trends in fish populations
of study area rivers through time. However, as with any sampling method,
lock chamber rotenone study results undoubtedly present a biased view of
the fishery of a stream reach for shoreline inhabiting species are
undoubtedly underrepresented.
With enactment of the National Environmental Policy Act (NEPA) of
1969, Environmental Impact Statements were required to be prepared for new
construction projects along the Ohio River. The Federal Water Pollution
Control Act of 1972, and its amendments PL 92-500, established a national
goal of eliminating the discharge of pollutants into all navigable waters
by 1985. f Subsections 316(a) and 316(b) of PL 92-500 required electric
utilities to evaluate the effects of cooling water withdrawals and
discharges of thermal effluents to the biota of source water rivers.
Enactment of NEPA and PL 92-500 has resulted in numerous site specific
biological studies along the Allegheny, Monongahela, and upper Ohio Rivers
between 1970 and 1983. Information concerning the composition of the fish
community at various locations along the shorelines of study area rivers
has, for the most part, been ignored in previous summaries (Krumholz 1981;
70
-------
Preston and White 1978; Pearson and Kruraholz 1984). The results of the
latter are included in the following discussion.
Characterization of the fishery of the Allegheny, Monongahela, and
upper Ohio Rivers will focus on the last 27 years. Prior to 1957,
improperly treated sewage and industrial wastes, coupled with low pH acid
mine drainage, influenced fish populations dramatically in the study area
(Lachner 1956; Krumholz 1981; ORSANCO 1962). Recent results from lock
chamber rotenone studies will be summarized for each study river (Tables
3-7, 3-8, and 3-9), and in discrete time periods—1957-1960, 1967-1970,
1974-1978, 1978-1980, 1981-1983. Where additional site specific studies
are available, these will be summarized for the appropriate time period.
This will be followed by an overview.
1957-1960
Ohio River (RM 0-200)
Lock Chamber Rotenone Studies. Twenty-two samples were taken during
this period and resulted in the collection of 60 species distributed among
209,068 individuals (Table 3-7). Emerald shiner (Notropis atherinoides)
numerically dominated (84.8%) and was followed by mimic shiner (N.
volucellus) (8.4%), black bullhead (Ictalurus melas) (3.3%), channel
catfish (I. punctatus) (1.1%), and sand shiner QJ. stramineus) (0.8%).
Overall, the 20 species of cyprinids collected accounted for 95.0 percent
of individuals (Table 3-7) and 66.0 percent of the bioraass (993.12 kg).
Five species—carp, emerald shiner, black bullhead, channel catfish, and
gizzard shad—comprised 90.5 percent of the total biomass.
Allegheny and Monongahela Rivers
All Methods. Nearly 90 percent of all fishes taken were mimic shiners
and emerald shiners, and these two species, together with the trout-perch
(Percopsis omiscomaycus) and the rosyface shiner (Notropis rubellus),
contributed more than 96 percent of the total numbers of fishes taken.
However, in total weight, the carp contributed 34.3 percent, the white
sucker (Catostomus commersoni) 20.2 percent, the emerald shiner 10.4 per-
71
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Table 3-7. Fish collected during Ohio River lock chamber
through 1983.
1957 - 1960 1967 - 1970'
No. K£. No. Kg[.
Lampreys
Ohio lamprey
— —
— —
Paddlefishes
Paddlefish
1
4.15
Gars
Longnose gar
— —
—
— —
— —
Eels
American eel
5
0.31
Herrings
Skipjack herring
104
23.23
19
1.89
Alewife
—
—
—
—
Gizzard shad
307
33.95
8,036
230.13
Mooneyes
Goldeye
5
0.95
"
Pikes
Muskellunge
—
—
Tiger musky
— —
—1"•
Minnows and Carps
Central stoneroller
3
0.02
Goldfish
14
2.06
6
1.52
Carp
699
432.07
5,483
1076.24
Silverjaw minnow
1
0.01
—
—
Bigeye chub
29
0.04
—
—
Silver chub
573
4.53
5
0.09
Golden shiner
17
0.08
25
0.63
rotenone studies, Ohio River Miles 0-200, from 1967
1974 - 1977a 1978 - 1980a 1981 - 1983b
No. K£.
No. Kg. No.
M.-
0.02
3 1.60 19
1 0.09 8
17 2.93 33
1 0.01
9,506 219.34 1,833
8.24 7 2.36
0.30
3.07 6 0.31
91.96 76,773 1016.11
2.22
0.22
0.88
1.38
5 1.32 1 0.27
2,127 997.54 1,682 788.50 4,047 5074.97
13
0.09
78
3
0.15
0.08
29
1
0.53
0.04
-------
Table 3-7. (continued)
1957
- 1960 a
1967
- 1970 a
1974 -
1977 a
1978 -
1980a
1981 -
1983 b
No.
No.
M-
No.
M-
No.
Kg.'
No.
M-
nnows and Carps (cont
.)
Emerald shiner 177,358
195.59
44,194
115.53
94,044
147.44
44,633
47.89
187,389
443.89
River shiner
67
0.03
16
0.04
2
0.01
2
0.01
—
—
Bigeye shiner
—
—
—
—
15
0.02
—
—
—
—
Ghost shiner
31
0.04
7
0.02
139
0.06
423
0.31
—
—
Striped shiner
9
0.01
—
—
—
—
—
—
—
—
Common shiner
83
0.14
1
0.01
—
—
—
—
—
—
Spottail shiner
—
—
—
—
—
—
1
0.01
—
—
Silver shiner
7
0.01
—
—
—
—
—
—
—
—
Rosyface shiner
24
0.02
1
0.01
—
—
—
—
—
—
Spotfin shiner
66
0.12
593
1.23
167
0.27
24
0.03
—
—
Sand shiner
1,740
1.97
373
0.60
258
0.26
152
0.09
1,346
0.73
Mimic shiner
17,581
18.04
1,962
2.66
5,978
7.04
13,625
5.69
6,524
4.24
Bluntnose minnow
343
0.52
4,731
8.04
209
0.22
407
0.35
92
0.10
Bullhead minnow
6
0.01
—
—
—
—
—
—
—
—
Creek chub
2
0.01
1
0.01
—
—
—
—
—
—
Unidentified shiners
—
—
18,464
62.23
—
—
—
—
116,911
119.61
jckers
River carpsucker
6
1.79
—
—
5
2.92
2
1.60
26
18.77
Quillback carpsucker
3
0.43
3
0.66
3
1.31
4
2.65
21
15.95
White sucker
105
0.88
7
0.63
9
1.35
19
4.89
4
0.85
Smallmouth buffalo
4
1.66
4
3.17
3
4.99
5
4.36
2
3.12
Bigmouth buffalo
—
—
—
—
—
—
1
6.36
—
—
Spotted sucker
8
1.29
1
0.12
3
, 1.25
22
6.85
50
22.53
Silver redhorse
4
0.43
—
—
—
—
—
—
1
0.15
River redhorse
—
—
—
—
—
—
—
—
1
0.58
Black redhorse
15
1.98
2
0.35
8
1.66
6
2.48
—
—
Golden redhorse
18
1.32
1
0.36
7
1.47
15
3.59
11
3.51
Shorthead redhor9e
—
—
—
—
—
—
3
0.58
9
9.64
Unidentified buffalo
—
—
—
—
--
—
—
—
74
97.64
reshwater catfishes
White catfish
—
—
570
9.41
542
10.41
77
14.57
17
2.74
Black bullhead
6,896
146.39
15
4.59
—
—
—
—
1
0.52
-------
Table 3-7. (continued)
1957 - I9603
1967 - 1970a
No.
M-
No.
Kg-
Freshwater catfishes (cont
.)
Yellow bullhead
3
0.14
491
13.20
Brown bullhead
431
12.56
4,309
156.32
Channel catfish 2,
283
91.00
5,504
164.86
Mountain madtom
1
0.02
—
—
Stonecat
—
—
1
0.01
Tadpole madtom
2
0.01
—
—
Brindled madtom
1
0.01
—
—
Flathead catfish
8
1.42
1
0.80
Unidentified bullheads
—
—
—
—
Troutperches
Troutperch
6
0.02
—
—
Silversides
Brook silverside
—
—
1
0.01
Killifishes
Banded killifish
2
0.01
2
0.02
Temperate basses
White bass
4
0.85
—
—
Striped bass
—
—
—
—
Sunfishes
Rock bass
7
0.07
5
0.04
Green sunfish
31
0.45
162
2.85
Pumpkinseed
11
0.29
210
2.69
Warmouth
6
0.27
1
0.01
Orangespotted sunfish
5
0.03
14
0.18
Bluegill
46
1.51
214
4.17
Longear sunfish
8
1.04
7
0.17
Redear sunfish
1
0.01
18
0.25
Smallmouth bass
3
0.04
2
0.13
Spotted bass
19
0.96
346
27.65
Largemouth bass
10
1.49
61
11.16
1974 - 1977*
No.
1978 - 1980c
Kg. No. Kg^.
1981 - 1983b
No. Kg.
81 4.60 100 8.27 32 0.93
752 62.12 284 22.55 28 4.97
2,566 157.23 2,491 196.99 2,416 188.71
5 0.06
22
8.83
18 17.10
81 25.48
2 0.30
0.01
40 0.09
0.01
1 0.01
18
2
0.93
0.03
41
3.22
140
22
12.61
0.98
2
17
20
1
44
61
9
0.11
0.49
0.12
0.07
0.18
1.59
0.19
3
5
2
1
2
61
2
0.19
0.03
0.04
0.01
0.01
1.31
0.01
8
6
4
11
73
0.82
0.05
0.15
0.04
1.18
2
107
37
0.10
15.06
5.60
4
29
14
0.07
3.11
1.90
14
132
14
1.54
15.72
3.62
-------
Table 3-7. (continued)
1957 - 1960a 1967 - 1970a 1974 - 1977a 1978 - 1980a 1981 - 1983b
No. Kg. No. Kg. No. Kg. No. Kg. No. Kg.
Sunfishe9 (cont.)
White crappie 26 1.52 231 2.96 99 3.83 151 9.04 281 14.11
Black crappie 6 0.56 221 7.66 25 1.99 13 1.89 80 5.94
Perches
Johnny darter — — — — 1 0.01 1 0.01
Yellow perch 4 0.24 1 0.05 32 1.48 7 0.38 3 0.13
Logperch 1 0.01 5 0.07 3 0.03 3 0.02 2 0.01
Channel darter — — — — 1 0.01 — — — —
Sauger — — 2 1.58 39 10.69 46 8.98 76 19.70
Walleye I 1.18 10 5.58 1 0.77 13 4.14 76 30.97
Drums
Freshwater drum 13 3.64 22 1.59 57 16.03 379 47.89 5,328 263.98
Totals 209,068 993.12 96,366 1924.49 117,068 1697.92 66,796 1322.44 325,403 7433.10
No. of chambers sampled 22 18 8 11 13
No. of species 60 51 51 54 46
aData for time periods 1957-1960, 1967-1970, 1974-1977, and 1978-1980 were compiled from Pearson and
Krumholz 1984.
^Data for 1981-1983 were compiled from unpublished 0RSANC0 data.
-------
Table 3-8. Fish collected during Allegheny River lock chamber rotenone studies, Allegheny River Locks No. 3
and 8, from 1967 through 1983.
Taxon
Eels
American eel
Herrings
Gizzard shad
Pikes
Muskellunge
Minnows and Carps
Carp
Bigeye chub
Golden shiner
Emerald shiner
Common shiner
Spottail shiner
Rosyface shiner
Sand shiner
Mimic shiner
Bluntnose minnow
Suckers
Quillback carpsucker
White sucker
Silver redhorse
Black redhorse
Golden redhorse
Shorthead redhorse
Freshwater catfishes
Yellow bullhead
Brown bullhead
Channel catfish
Stonecat
1967 - 1970 1974 - 1977
No. Kg. No. Kg.
6 0.44
1 2.27
59 31.40
48 0.05
1 0.04
15,893 14.70
25 0.03
1 0.01
6,387 5.84
151 0.16
4 2.83
1 0.36
6 0.93
7 2.02
1 0.20
16 0.13
80 10.95
85 10.24
1978 - 1980 1981-1983
No. Kg. No. Kg.
2 0.30
33 4.36 136 6.66
1 0.70
60 43.20 6 4.35
1 0.01
319 0.50
1 <0.01
3 0.03
1 <0.01
194 0.22
5 0.01
6 3.02
1 <0.01
2 0.70
2 0.75
10 0.97
4 0.90
1 <0.01
197 25.08 80 9.43
8 0.01 2 0.01
-------
Table 3-8. (continued)
1967 - 1970 1974 - 1977 1978 - 1980 1981-1983
Taxon No. Kg. No. Kg. No. Kg. No. Kg.
Freshwater catfish (cont.)
Tadpole raadtom — — — — 1 <0.01 —
Flathead catfish 29 1.52 — — 50 3.69 4 0.15
Troutperches
Troutperch 121 0.29 — — 703 1.73 12 0.01
Sunfishes
Rock bass 22 0.60 — — 2 0.01 2 0.06
Green sunfish 1 0.01 — — — — — —
Pumpkinseed 5 0.02 — — 1 0.06 — —
Bluegill 9 0.11 — — 5 0.04
Smallmouth bass 6 0.21 — — 2 0.65 2 0.24
Spotted bass — — — — — — 4 0.67
Largeinouth bass 2 0.01 — — —
White crappie — — — — 8 0.64 — —
Black crappie 7 0.59 — — — —
Perches
Rainbow darter — — — —• 1 <0.01 —
Johnny darter 4 0.01 — — 13 0.01
Yellow perch 1 0.01 — — 6 0.06 —
Logperch 10 0.05 — — 13 0.10 3 0.01
Sanger — — — -- 1 0.25 — —
Walleye 12 1.78 — — 18 2.54 15 4.27
Drums
Freshwater drum — — — — 1 0.60 28 1.97
Totals 23,001 87.81 — — 1,665 90.16 305 28.81
No. of chambers sampled 4 0 3 2
No. of species 31 0 33 14
-------
Table 3-9. Fish collected during Monongahela River lock chamber rotenone studies, Monongahela River Lock No.
2 and Maxwell Lock, from 1967 through 1983.
1967 -
1970
1973 -
1977
1978
- 1980
1981-
1983
Taxon
No.
Kg-
No.
M-
No.
Kg.
No.
M-
Herrings
Gizzard shad
18
2.32
983
34.74
45
9.43
681
9.67
Minnows and Carps
Goldfish
—
—
7
0.47
2
0.34
—
—
Carp
143
20.35
2,403
157.96
691
286.28
194
106.81
Golden shiner
—
—
1
0.03
2
0.02
—
—
Emerald shiner
129
0.30
4,742
8.75
6,768
4.95
—
—
River shiner
—
—
1
<0.01
—
—
—
—
Spotfin shiner
—
—
22
0.05
3
0.01
—
—
Sand shiner
—
—
153
0.16
7
0.01
—
—
Mimic shiner
4
<0.01
18
0.03
64
0.03
—
—
Bluntnose minnow
3
0.01
42
0.06
66
0.13
—
—
Fathead minnow
1
0.01
—
—
—
—
—
—
Creek chub
—
—
—
—
1
<0.01
—
—
Suckers
Quillback carpsucker
—
—
1
0.38
3
2.10
—
—
White sucker
1
0.05
3
0.55
—
—
—
—
Silver redhorse
—
—
1
0.34
—
—
—
—
River redhorse
—
—
—
—
—
—
2
0.36
Black redhorse
—
—
6
1.10
—
—
—
—
Golden redhorse
1
0.47
1
0.09
1
0.25
4
0.74
Redhorse
—
—
—
—
1
0.29
—
—
Freshwater catfishes
White catfish
—
—
9
0.59
15
1.40
2
0.10
Yellow bullhead
1
0.01
78
0.43
15
0.07
—
—
Brown bullhead
180
11.71
713
18.90
22
0.80
—
—
Channel catfish
2
0.02
1,317
42.02
699
32.84
548
38.51
Flathead catfish
—
—
4
0.02
3
1.81
5
0.92
-------
Table 3-9. (continued)
1967 - 1970 1973 - 1977 1978 - 1980 1981-1983
Taxon No. Kg. No. Kg. No. Kg. No. Kg.
Troutperches
Troutperch — — — — 6 0.02 —
Sunfishes
Rock bass — — 31 0.09 — — —
Green sunfish 13 0.19 6 0.08 2 0.06 —
Pumpkinseed 7 0.19 68 0.63 6 0.06 2 0.06
War mouth — — 1 0.01 — — — —
Orangespotted sunfish 2 0.04 5 0.01 — — —
Bluegill 14 0.12 733 1.95 6 0.20
Redear sunfish — — — — 1 0.01 —
Smallraouth bass — — 6 0.48 1 0.01 1 0.03
Largemouth bass 3 0.69 295 15.37 2 0.30 — —
White crappie — — 6 0.50 7 0.86 1 0.26
Black crappie — — 6 0.63 1 0.16 —
Perches
Johnny darter — — 3 <0.01 —
Logperch — — — — 1 <0.01 —
Sauger — — 1 0.45 — — — —
Walleye — — — — 15 9.62 9 7.44
Drums
Freshwater drum — — — — 2 1.16 146 3.39
Totals 522 36.48 11,666 286.87 8,458 353.22 1,595 168.29
No. of chambers sampled 4 6 3 2
No. of species 16 32 30 12
-------
cent, the golden redhorse (Moxostoma erythrurum) 5.3 percent, and the mimic
shiner 4.9 percent of the total catch.
1967-1970
Ohio River (RM 0-200)
Lock Chamber Rotenone Studies. Between 1967 and 1970, lock chamber
studies were conducted and yielded a total of 96,366 individuals, 51
species, and 1925.20 kg of biomass (Table 3-7). The 10 most abundant
species during this time period were: emerald shiner (45.9%), unidentified
shiners (16.2%), gizzard shad (8.3%), carp (5.7%), channel catfish (5.7%),
bluntnose minnow (Pimephales notatus) (4.9%), brown bullhead (I_. nebu-
losus) (4.5%), mimic shiner (2.0%), spotfin shiner (Notropis spilopterus)
(0.6%), and yellow bullhead (][. natalis) (0.5%). The 14 species of
cyprinids, plus unidentifiables, accounted for a large percentage of the
individuals collected (78.7%) during this time period as in the 1957-1960
time period. Carp, gizzard shad, channel catfish, brown bullhead, and
emerald shiner yielded highest biomass at 1,076.24, 230.13, 164.86, 156.32,
and 115.53 kg, respectively. These five species comprised 90.5% of the
total biomass collected during this sampling period.
Allegheny River
Lock Chamber Rotenone Studies. During this time period Allegheny
River Locks No. 3 and 8 were each sampled twice. This resulted in the
collection of 23,001 individuals, 31 species, and 87.81 kg of biomass.
Cyprinids accounted for 98.1% of all individuals collected (Table 3-8) and
59.5% of the biomass. The 10 numerical dominants were: emerald shiner
(69.1%), mimic shiner (27.8%), bluntnose minnow (0.7%), trout-perch (0.5%),
channel catfish (0.4%), brown bullhead (0.3%), carp (0.3%), bigeye shiner
(hi. boops) (0.2%), flathead catfish (0.1%), and the rosyface shiner
(0.1%).
Monongahela River
Lock Chamber Rotenone Studies. Monongahela River Lock No. 2 and
80
-------
Maxwell Lock were each sampled twice during this study period and yielded a
total of 522 fish distributed among 16 species. The three most abundant
species were the brown bullhead (34.4%), the carp (27.4%), and the emerald
shiner (24.7%); no other species comprised more than 3.5% of the total.
Carp and brown bullhead comprised 87.0% of the 36.84 kg of biomass
collected.
1974-1977
Ohio River (RM 0-200)
Lock Chamber Rotenone Studies. Eight lock chamber studies were
conducted along the upper Ohio River from 1974 through 1977 yielding
117,068 fish, 51 species, and 1697.92 kg biomass (Table 3-7). Cyprinids
continued to numerically dominate, accounting for 87.9% of the total. The
10 most abundant species were: emerald shiner (80.3%), gizzard shad
(8.1%), mimic shiner (5.1%), channel catfish (2.2%), carp (1.8%), brown
bullhead (0.6%), white catfish (0.5%), sand shiner (0.2%), bluntnose minnow
(0.2%), and spotfin shiner (0.1%). Of the biomass, 93.4% of the total was
made up by five species—carp (58.8%), gizzard shad (12.9%), channel
catfish (9.3%), emerald shiner (8.7%), and brown bullhead (3.7%).
Other Studies. During this study period, Ohio River fisheries surveys
or impingement sampling was conducted at power plants located at the
following Ohio River miles: 34.9, 53.9, 57.5, 102.5, and 160.5. A summary
of the catch at each of these sites follows.
Gill netting and impingement sampling were conducted at the Willow
Island Power Plant (RM 160.5) from August 1973 through August 1974. Gill
netting yielded 773 fish; this catch was dominated by the following five
species: spotted bass (64.6%) (Micropterus punctulatus), gizzard shad
(9.3%), carp (6.7%), channel catfish (5.4%), and brown bullhead (3.9%).
All other species comprised <2.6% of the catch in this shoreline sampling.
During this period, 30 species and 2,615 individuals were impinged by the
Willow Island Power Plant. Channel catfish, gizzard shad, bluegill,
(Lepomis macrochirus), emerald shiner, and white crappie (Pomoxis
81
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annularis) comprised 94.6% of all fish impinged and 65.3% of the biomass
(Monongahela Power Company 1976).
A total of 1,301 fish were collected from the Ohio River near the
Toronto Power Plant (RM 57.5) in November 1974 during sampling using gill
nets, hoop nets, and electrofishing. The community was dominated by
emerald shiner, carp, gizzard shad, bluntnose minnow, sand shiner, and
largemouth bass (M. salmoides) which comprised 94.9% of the catch.
Twenty-five species were collected during the survey (Westinghouse 1974).
Two fish surveys, one in August 1974 and the second in July 1975, were
conducted near the Burger Power Plant (RM 102.5) to describe the fish
community at this location. Fish were sampled using gill and hoop nets and
electrofishing. The 1974 survey yielded only 45 fish distributed among 12
species; this catch was dominated by spotted bass, channel catfish, carp,
gizzard shad, and longnose gar (Lepisosteus osseus). The 1975 survey
yielded 20 species and 383 fish. Species numerically dominating included
spotfin shiner, bluntnose minnow, sand shiner, emerald shiner, and carp,
which together comprised 88.0% of the catch. No other species collected
during the latter survey comprised more than 4.0% of the total (Westing-
house 1975).
Preoperational baseline aquatic ecological studies for Duquesne Light
Company's Beaver Valley Power Station, located at Ohio River Mile 34.9,
were conducted from 1972 through 1976 and are summarized here (NUS Corpora-
tion 1976). A total of 2,488 fish were collected from transects 1, 2, 2B,
and 3 beween 1972 and 1975, representing seven families and 34 species.
The catch was numerically dominated by the cyprinids emerald shiner
(43.2%), sand shiner (20.9%), bluntnose minnow (14.1%), carp (4.9%), and
the channel catfish (4.9%); these five species made up 87.9% of the total
catch over the three year period. Nineteen of the remaining 29 species
were represented by 10 or fewer individuals (NUS Corporation 1975).
During 1975, fish were sampled using gill nets, electrofishing, and by
trawling during August, September, October, and November near the Beaver
Valley Power Station. During this period, 1,661 fish were collected
-------
representing seven families and 23 species. Three species, emerald shiner,
sand shiner, and bluntnose minnow, accounted for 89.7 7. of the fishes
collected. Channel catfish (2.7%) and yellow perch (Perca flavescens)
(1.6%) were the next most abundant species (NUS Corporation 1975).
Fish populations near the Beaver Valley Power Station were sampled
monthly from May through September and again in November 1976, using gill
nets and electrofishing apparatus. This sampling resulted in the collec-
tion of 837 fish consisting of 27 species representing seven families.
Emerald shiner, sand shiner, and bluntnose minnow dominated the collec-
tions, accounting for 79% of the total catch. Other abundant species were
carp, gizzard shad, channel catfish, and yellow perch (Duquesne Light
Company 1976).
Ohio Edison initiated annual fish sampling surveys in the vicinity of
the W.H. Sammis Plant (Ohio River Mile 53.9) in 1973 to assess fish commu-
nity structure; these studies have been conducted annually through 1982 and
provide a continuous record of change in the composition of the community
at this location along the Ohio River. The fishes near this plant were
sampled using a variety of methods including electrofishing, gill and hoop
netting, trawling, and beach seining, although not all methods were used
each year. Table 3-10 presents an overview of the 10 most abundant species
collected from this location each year from 1973 through 1982, the total
number of individuals collected, and the percentage of the total catch
comprised by the community dominants° Over the ten-year period, 23 differ-
ent taxa occurred among the most numerous species; however, only two
species—emerald shiner and carp—were among the top 10 each year. Species
among the top 10 during each of 5 or more years included gizzard shad,
bluntnose minnow, sand shiner, spotted bass, and channel catfish (Table
3-10). Species that were among the top 10 during only one or two years
included white crappie, goldfish, white sucker, Johnny darter (Etheostoma
nigrum), green sunfish (Lepomis cyanellus), ghost shiner (Notropis
buchanani), and freshwater drum. The ten most abundant species accounted
for ,79.7-99.4% of the individuals collected during a year. Species
displaying dramatic changes in abundance through time included the gizzard
shad, emerald shiner, carp, bluntnose minnow, sand shiner, and pumpkinseed
83
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Table 3-10. The results of annual fish sampling near the W.H. Sammis Plant
(Ohio River Mile 53.9). Tabular values present ten most abundant
species in the catch from 1973 through 1982, the total number of
fish collected, the percentage of the total catch the top ten
species comprised, and the total number of species collected.a»^
Species
1973
1974
1975
1976
1977
1978
1979
1980
1981
1982
Gizzard shad
1
2
2
4
—
—
9
8
2
5
Emerald shiner
2
1
1
6
9
4
4
3
1
1
Largeraouth bass
3
3
4
7
-
-
-
-
-
-
Carp
4
4
6
1
3
7
8
5
5
6
Pumpkinseed
5
7
9
-
10
-
-
-
-
-
Bluegill
6
6
-
-
-
9
-
-
-
-
White crappie
7
-
-
-
-
-
-
10
-
-
Goldfish
8
10
-
-
-
-
-
-
-
-
Smallmouth bass
9
8
-
5
-
-
-
-
-
-
Logperch
10
-
8
8
-
-
-
-
-
-
Bluntnose minnow
-
5
3
2
1
1
6
2
3
3
White sucker
-
9
-
-
8
-
-
-
-
-
Sand shiner
-
-
5
3
2
3
10
7
7
2
Spotfin shiner
-
-
7
10
-
-
-
-
6
9
Spotted bass
-
-
10
9
-
8
-
9
8
10
Trout-perch
-
-
-
-
4
5
2
-
-
-
Mimic shiner
-
-
-
-
5
-
5
4
-
4
Johnny darter
-
-
-
-
6
-
-
-
-
-
Channel catfish
-
-
-
-
7
6
3
6
10
7
Shiner YOY
-
-
-
-
-
2
7
1
9
-
Green sunfish
-
-
-
-
-
10
-
-
-
-
Ghost shiner
-
-
-
-
-
-
1
-
4
-
Freshwater drum
-
-
-
-
-
-
-
-
-
8
Total catch
1889
19466
2346
444
16110
5417
3238
7783
2127
9555
Top 10 species -
% of total
98.6
99.4
92.9
79.7
96.8
90.7
82.6
94.1
88.7
95.4
No. of species
collected
23
32
35
41
45
44
51
40
39
50
aSampling methods included electrofishing, gill and hoop netting, trawling,
and beach seining. Not all methods were used each year.
bSources: WAPORA, Inc. 1974, 1975, 1976, 1977, 1978, 1979, 1980, 1981;
Geo-Marine, Inc. 1982, 1983.
34
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(L. gibbosus). Over recent years, sport and commercial species, i.e.,
channel catfish, spotted bass, and freshwater drum appeared to be
increasing in abundance whereas largemouth bass, bluegill, and pumpkinseed
decreased.
Allegheny River
Lock Chamber Rotenone Studies. None were conducted during this study
period.
Other Studies. During the preparation of a 316(a) demonstration for
Duquesne Light Company's Cheswick Power Station, the fish of the Allegheny
River between River Miles 14.0 and 18.5 were sampled by electrofishing and
gill and hoop netting during August 1975. This sampling yielded 237
individuals distributed among 20 species and having a biomass of 45.5 kg.
The catch was numerically dominated by emerald shiner (41.7%), bigeye
shiner (14.8%), carp (8.9%), pumpkinseed (8.0%), and northern hog sucker
(Hypentelium nigricans) (6.8%); these five species comprised 87.2% of the
biomass. No other species accounted for more than 4.0% of the catch in
terms of either numbers or biomass.
As part of an environmental assessment regarding the impacts associ-
ated with commercial sand and gravel dredging operations in the Allegheny
River, the Pittsburgh District Army Corps of Engineers sponsored fisheries
studies during 1975 and 1977. Fish were collected in pools 3, 5, and 7 in
1975 by electrof ishing and in pools 3 and 7 in 1977 by electrof ishing,
experimental gill netting, and seining. The combined catch over the entire
study was 4,931 fish and 44 species; electrofishing, seining, and gill
netting yielded 3,849; 868; and 214 fish, respectively. Species dominating
the electrofishing catch included emerald shiner (53.3%), mimic shiner
(23.9%), bluntnose minnow (6.2%), trout-perch (3.4%), and smallmouth bass
(Micropterus dolomieui) (2.1%); overall, cyprinids comprised the majority
of the catch, 87.9%. Species dominating the gill netting catch included
carp, rockbass (Ambloplites rupestris), brown bullhead, quillback
(Carpiodes cyprinus), channel catfish, and walleye (Stizostedion vitreum)
85
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which together accounted for 83.7% of the total. The shoreline seining
catch was numerically dominated by minnows and shiners (95.6%).
Allegheny River fish surveys were conducted in April 1977 concurrently
with impingement sampling occurring at West Penn Power Company's Armstrong
Power Station, Allegheny River Mile 55.4. River fish surveys were
conducted on April 26-27, 1977 using electrofishing apparatus and gill and
baited hoop nets; this sampling yielded 736 fish representing 21 species
and having a biomass of 60.9 kg. Rosyface shiner (59.2% of total number of
fish collected), golden redhorse (11.1%), sand shiner (11.1%), bluntnose
minnow (5.7%), and smallmouth bass (3.4%) were the more abundant species in
the catch. Carp and golden redhorses comprised the greatest portion of the
total fish biomass (39.6% of the total biomass and 36.7%, respectively).
Impingement sampling was conducted from November 1976 through October 1977
and resulted in the collection of 31 species, 509 individuals, and a
biomass of 4.81 kg. The more abundant fish species in impingement were
trout-perch (22.4%), unidentifiable redhorses (16.5%), white crappie
(11.6%), emerald shiner (7.1%), and golden redhorse (5.5%); all other
species comprised less than 5% of the fish impinged (Energy Impact
Associates, Inc. 1978).
Monongahela River
Lock Chamber Rotenone Studies. From 1973 to 1977, six lock chamber
studies were conducted along the Monongahela River; these studies yielded
11,666 fish distributed among 32 species. Six species—emerald shiner,
carp, channel catfish, gizzard shad, bluegill, and brown bullhead—together
accounted for 93.3% of the total; none of the remaining species accounted
for more than 2.5% of the numerical catch. Of the 286.87 kg of biomass,
carp, channel catfish, gizzard shad, and brown bullhead comprised 88.4%
(Table 3-9).
1978-1980
Ohio River (RM 0-200)
Lock Chamber Rotenone Studies. Cyprinids continued to numerically
86
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dominate the catch of the upper Ohio River, accounting for 91.4% of the
66,807 individuals collected. The 10 most abundant species during this
study period were: emerald shiner (66.8%), mimic shiner (20.4%), channel
catfish (3.7%), gizzard shad (2.7%), carp (2.5%), ghost shiner (0.6%),
freshwater drum (0.6%), brown bullhead (0.4%), white crappie (0.2%), and
yellow bullhead (0.1%). Carp, channel catfish, gizzard shad, emerald
shiner, and freshwater drum comprised 88.7% of the 1,322.44 kg biomass
collected. During this study period, 54 species were collected (Table
3-7).
Other Studies. Eighteen impingement samples were collected for the
preparation of a 316(b) demonstration for the Frank R. Phillips Power
Station (Ohio River Mile 15.2) between January 1 and December 31, 1978.
This sampling yielded 1,030 fish representing 35 species and nine families;
the total biomass was 12.9 kg. The emerald shiner was the most abundant
species impinged, accounting for 47.5% of the total number. Next in
numerical dominance were channel catfish, bluegill, white crappie, mimic
shiner, gizzard shad, and sand shiner, which each accounted for 9.1, 8.0,
6.0, 5.8, 5.3, and 4.3%, respectively, of the total. Together, these seven
species accounted for 86.0% of the total number of fish impinged, and 39.0%
of the biomass. Carp catch yielded highest biomass (34.0%). Of the
remaining 28 species impinged, 23 were represented by 5 or less fish, and
17 species were comprised of 2 or less individuals (Equitable Environmental
Health, Inc. 1979a).
Fourteen impingement samples were collected from the Shippingport
Atomic Power Station (Ohio River Mile 35.0) between January 1 and December
31, 1978, and resulted in the collection of 24 species representing eight
families of fishes. The samples were dominated by cyprinids which
accounted for 63.8% of the total catch (939 fish collected) and 25% of the
7.0 kg total biomass. The emerald shiner was the most numerous species
impinged, making up 59.0% of the numerical catch but only 15.3% of the
biomass. Gizzard shad represented 20.9% of the numerical catch and 42.2%
of the biomass. Bluegill, channel catfish, and white bass (Morone
chrysops) were next in numerical dominance, representing 8.4, 2.7, and
1.8%, respectively, of the catch; these three species comprised 23.9% of
87
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the total bioraass impinged. All other species collected represented only
7% of the total number and 5% of the bioraass. Seventeen taxa were repre-
sented by 10 or fewer individuals and 13 of these had 2 or less individuals
(Equitable Environmental Health, Inc. 1979b).
Impingement sampling was also conducted from May 1978 through May 1979
at the Cardinal Plant (Ohio River Mile 76.5). During this study, 39
impingement samples were collected and yielded a total of 12,772 fish
representing 43 species and 11 families. The total weight of all fish
impinged was approximately 226.6 kg. Four species, the gizzard shad (63.5%
of total number), emerald shiner (14.1%), white crappie (7.8%), and channel
catfish (6.4%), accounted for 91.8% of the total number of fish collected.
Twenty-two species were represented by 10 or fewer individuals, and nine
species had 2 or less individuals. Four species represented 85.1% of the
bioraass: gizzard shad (62.1% of total weight), carp (10.0%), channel
catfish (8.8%), and white crappie (4.2%) (NUS Corporation 1979b).
Fisheries monitoring continued at the Beaver Valley Power Station in
1978 with electrofishing, gill netting, and seining being conducted from
May through September and again in November. This sampling yielded 2,329
fish representing 34 species, 10 families, and one hybrid. The catch was
dominated by the following species of cyprinids: sand shiner (37.0%),
emerald shiner (31.3%), bluntnose minnow (16.6%), and carp (6.1%). No
other species comprised more than 1.5% of the catch during 1978 and 24
species and the hybrid were each represented by 10 or fewer individuals in
the catch.
During 1979, adult fish surveys were performed once per month, from
May through September, and in November near the Beaver Valley Power
Station. During each survey, fish samples were collected at three study
area transects using gill nets, electrofishing gear, trawls, and seines.
Cyprinids continued to dominate the catch numerically with sand shiner,
bluntnose minnow, emerald shiner, and mimic shiner comprising 97.2% of the
total. None of the other 29 species collected accounted for more than 0.5%
of the fish collected, and 23 species were represented by 10 or fewer
individuals in the combined catch.
88
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Annual fisheries studies were initiated at the Cardinal Plant (Ohio
River Mile 76.7) in 1978 and were conducted through 1982. Fish sampling
was conducted by trawling, electrofishing, gill and hoop netting, and beach
seining (WAPORA, Inc. 1979, 1980, 1981; Geo-Marine, Inc. 1982, 1983). The
results of these surveys indicated that the shoreline fishery at this
location was numerically dominated by cyprinids, particularly emerald
shiner, sand shiner, bluntnose minnow, spotfin shiner, mimic shiner,
striped shiner (Notropis chrysocephalus), and carp, as the following
overview, which lists the top ten species per year in terms of numerical
abundance, shows:
Taxon/Year
1978
1979
1980
1981
1982
Shiner YOY
1
2
6
—
—
Bluntnose minnow
2
1
1
2
2
Sand shiner
3
4
3
3
3
Emerald shiner
4
3
2
1
1
Carp
5
6
8
9
8
Channel catfish
6
7
8
9
8
Spotfin shiner
7
8
7
7
4
Striped shiner
8
9
-
-
-
Golden redhorse
9
-
-
-
-
Trout-perch
10
10
-
-
-
Mimic shiner
-
5
4
6
-
Cyprinidae (unid.)
-
-
5
-
-
Gizzard shad
-
-
9
4
5
Spotted bass
-
-
-
8
-
Smallmouth bass
-
-
-
10
-
Freshwater drum
-
-
-
-
6
White sucker
-
-
—
—
10
Total catch
6724
7523
12767
4148
12678
Top 10 species
% of total
97.0
95.2
96.2
95.1
97.7
Total species
40
43
44
38
41
Channel catfish was among the 10 most abundant species each year. The
following species were among the top 10 at some time, but not each year of
sampling: striped shiner, golden redhorse, trout-perch, mimic shiner,
gizzard shad, spotted bass, smallmouth bass, freshwater drum, and white
sucker. The increase in sport species in the catch during latter years is
particularly promising. During each year, the 10 most abundant species
comprised at least 95% of the total catch, while many of the other species
89
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in the catch during a particular year were represented by only a few
individuals.
Allegheny River
Lock Chamber Rotenone Studies. Thirty-three species of fish, 1,665
individuals, and 90.16 kg of biomass were collected during three lock
chamber surveys conducted along the Allegheny River between 1978-1980.
Trout-perch, emerald shiner, channel catfish, and mimic shiner comprised
84.9% of the numerical catch, and carp and channel catfish accounted for
75.7% of the biomass.
Monongahela River
Lock Chamber Rotenone Studies. Emerald shiner, channel catfish, and
carp comprised 96.5% of the 8,458 individuals and 91.7% of the 353.22 kg of
biomass collected during three lock chamber studies conducted along the
Monongahela River during this time period. Overall, 30 species were
collected (Table 3-9).
Other Studies. From October 1977 through September 1978 impingement
data were collected at Duquesne Light Company's Elrama Power Station,
Monongahela River Mile 25.0, for preparation of a 316(b) demonstration.
This power plant has a shoreflush intake, and the species impinged on the
plant's traveling screens would be representative of the fishery present in
shoreline regions along this river. A total of 8,199 fish representing 28
species and 38.81 kg biomass were collected. Species that numerically
dominated the catch included the bluegill (69.9%), pumpkinseed (12.6%),
gizzard shad (10.0%), emerald shiner (3.4%), and channel catfish (2.3%),
for a total of 98.2% of the catch. These species also comprised 88.1% of
the biomass (Ecological Analysts, Inc. 1978).
1981-1983
Ohio River (RM 0-200)
Lock Chamber Rotenone Studies. The catch for this study period,
90
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402,176 individuals and 7,433.09 kg biomass, was the highest recorded for
any of the study periods. Cyprinids continued to numerically dominate the
catch, accounting for 78.7% of the individuals collected. Among the 10
most abundant taxa collected were the following: emerald shiner (46.6%),
unidentified shiners (29.1%), gizzard shad (19.1%), mimic shiner (1.6%),
freshwater drum (1.3%), carp (1.0%), channel catfish (0.6%), sand shiner
(0.3%), white crappie (0.1%), and white bass (<0.1%). Carp, gizzard shad,
emerald shiner, freshwater drum, and channel catfish comprised 94.0% of the
total biomass. Overall, 46 species were collected during this period
(Table 3-7).
Allegheny River
Lock Chamber Rotenone Studies. Allegheny River L/D No. 3 was sampled
twice during this study period and yielded a total of 305 fish distributed
among 14 species and weighing 28.81 kg. Gizzard shad, channel catfish,
and walleye numerically dominated the catch (80.0% of the total), whereas
these three species plus carp comprised 85.8% of the biomass (Table 3-8).
Monongahela River
Lock Chamber Rotenone Studies. Two lock chamber studies were conduc-
ted at Monongahela River Lock Number 2 during this period; these yielded
1,595 fish distributed among 12 species and weighing 168.38 kg. Gizzard
shad, channel catfish, carp, and freshwater drum comprised 98.4% of the
numerical catch and 94.1% of the biomass. Nine walleye were collected and
accounted for 4.4% of the biomass.
Other Studies. 316(b) studies were conducted during 1981 and 1982 at
the Mitchell Power Station located at River Mile 29.4. That study yielded
a total of 415 individuals distributed among 16 species. Six species—
gizzard shad, freshwater drum, emerald shiner, channel catfish, bluegill,
and white crappie—comprised 93.4% of the catch, with each of the six
species accounting for 28.4, 22.4, 16.1, 11.1, 9.9, and 5.5%, respectively,
of the catch (NUS Corporation 1982).
91
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Overview
Historical summaries of the ecology and biota of the study area have
been provided by ORSANCO 1962, Trautman 1981, Kruraholz and Minckley 1964,
Pearson and Krumholz 1984, Krumholz 1981, Preston 1974, Preston and White
1978, Lachner 1956, and Westinghouse 1976. A brief overview of information
presented by the above authors follows.
Prior to European colonization of the study area the watershed of the
Allegheny River, Monongahela River, and upper Ohio River was forested with
a variety of forest types which contribute to the ecological stability of
the watershed. Soil erosion was minimal, seasonal variations in runoff and
water quality were dampened, and as a result the quality of water in the
major drainages was excellent (Westinghouse 1976, Trautman 1981, Pearson
and Kruraholz 1984). Remains recovered from Paleo-Indian habitation sites
in the lower Allegheny and Ohio River Valley reveal extensive use of, and
perhaps seasonal subsistence on, fishes and turtles taken from the river.
The physical characteristics of the pristine study area rivers can only be
deduced from the reports of early travelers in the region, who consistently
remarked on the beauty of these waters and noted the abundant fish life in
them (ORSANCO 1962, Trautman 1981, Krumholz 1981, Pearson and Krumholz
1984).
P.B. Sears (cited in Westinghouse 1976) described the history of the
white man's economy in the study region in three sections: pioneer-agri-
cultural phase (1770-1850), the industrial transition (1850-1900), and the
neo-technical-urban phase (1900 to present). These categories will be used
here to explain the changing ecology of the study area.
During the pioneer-agricultural phase the first changes were caused
primarily by the initial clearing of the land in the watershed of each of
the rivers. Deforestation, by clearing for farmlands, cutting for charcoal
to feed the scattered rural iron furnaces, and timbering for lumber and
mine props, proceeded rapidly in the lower reaches of the Allegheny River.
The impact of deforestation on the waters of these three rivers was
dramatic. Seasonal floods were augmented by increased runoff from denuded
92
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hillsides. Soil erosion inevitably followed, with the result that silt
loads in the waters were greatly increased. Scouring and siltation of the
main river channels proceeded rapidly with the increase in frequency and
severity of floods (Westinghouse 1976). For the most part, however, the
waters were normally clear, containing little soil in suspension except
during some freshets and floods. The bottoms of the waters were free of
clayey silts, and were largely composed of sand, gravel, boulders, bedrock,
and organic debris. The fish fauna was also one which required clear
waters, and clean bottoms of sand, gravel, boulders, and bedrock (Trautman
1981).
Baseline data for the fauna of the lower Allegheny, lower Monongahela,
and upper Ohio River during early European colonization are scanty.
Lachner (1956) listed approximately 125 species in 25 families as consti-
tuting the original fish fauna of the upper Ohio River Basin. Travelers
along the Ohio River in the late 1700's remarked on the abundance of
fishes. The catch included sturgeon, freshwater drum, walleye, sauger,
muskellunge, white catfish, American shad, blue sucker, blue catfish,
flathead catfish, and buffalo (0RSANC0 1962). Pike as large as 100 pounds
were taken and sturgeon and spoon-bill catfish (Polyodon spathula) were not
uncommon.
The immediate effect of deforestation on the fauna of the study area
was two-fold. Entire species, susceptible to increased silt-load in the
waters, were extirpated from the area. Fish species in this category
included the harelip sucker (Lagochila lacera), big-eye minnow, and creek
chubsucker (Erimyzon oblongus). The second event was replacement of the
extirpated species by adjustment in the silt-tolerant elements of the
fauna, to fill vacant niches and occupy depopulated habitats (Westinghouse
1976).
Comprehensive descriptions of the Ohio River made in 1818 and 1819
list depths varying from 3 feet at low water to 30 feet at high water. At
low stages the river was almost clear, with over 130 islands and numerous
sandbars identified. Fish species described numbered 60, of which 55 are
considered valid.
93
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In the 1800's the Ohio River began to change from a natural stream to
one influenced by the activity of man. Steamboats were introduced in 1811
and by 1832 there were approximately 230 operating. Near this time the
U.S. Army Corps of Engineers began to remove obstructions from the channel
and to construct dikes to improve river navigation. These activities
decreased the number of sandbars and gravel beds along the upper Ohio
River.
The industrial transitional phase (1850-1900) produced the most
profound impact on the aquatic fauna of the study area rivers. In addition
to the silt pollution that continued from the deforested and largely
agricultural watershed, the river was scourged by chemical pollution from
mines and industries, and by sewerage from the rapidly increasing human
population of the watershed. The Allegheny River became progressively
loaded with brines and oil from the wells and refineries in the Oil City-
Franklin area, whereas the Monongahela was influenced by acid mine drainage
in the upper portion of the basin, and industrial wastes in the lower basin
(Westinghouse 1976, Preston 1974). Added to the acid mine drainage were
pollutants from pulp mills, tanneries, steel manufacturing, and other
streamside industries. Between 1880 and 1900 the human population along
the Ohio River increased from 500,000 to 1,250,000. In 1900, only two
cities in the entire Ohio River Basin had sewage treatment plants; many
urban areas simply discharged their septage directly to the Ohio River.
Along with deterioration in water quality, the lower Allegheny River
was undergoing severe physical changes during this period. As the popula-
tion of communities along the river (particularly Pittsburgh and Allegheny)
increased, the river was progressively straightened and canalized. This
eliminated many peripheral aquatic habitats, such as oxbows, meanders, and
marshes. Increasing use of the river as a navigation channel also had its
effect. The original Lock and Dam Numbers 2 (at River Mile 6.7) and 3 (at
River Mile 14.5) were constructed during the period 1894 through 1908.
These dams created navigation pools, and eliminated all shallower-water
habitats, such as riffles, in the lower 20 miles of the Allegheny.
Finally, channel-maintenance dredging of the river was started during this
period. Dredging destroyed bottom fauna in the dredged sites, and contrib-
94
-------
uted to an increased silt-load in the water (Westinghouse 1976). The first
cross-channel dam on the Ohio River was constructed at Davis Island, 5
miles downstream of Pittsburgh in 1885. By 1911 there were 12 dams between
Pittsburgh and Parkersburg, West Virginia. These dams improved navigation,
but were barriers to fish migration (Pearson and Krumholz 1984, Trautman
1981).
The fauna of the study area was devastated during this period. The
fish fauna underwent profound changes during the period 1850-1900. Lachner
(1956) listed the following 18 species of fishes that were reported in the
upper portion of the Ohio River Basin in Pennsylvania prior to 1900, some
of them common or abundant, but which have not been reported in recent
years: paddlefish, lake sturgeon, shovelnose sturgeon, shortnose gar,
bowfin, goldeye, gizzard shad, smallmouth buffalo, highfin carpsucker,
river carpsucker, blue sucker, sturgeon sucker, river shiner, silvery
minnow, blue catfish, American eel, sauger, and freshwater drum. In addi-
tion to extirpation or reduction in distribution of these species, many of
them such as the pikes, walleyes, catfishes, buffalofishes, suckers, drum,
and sturgeons (desirable food or game fishes), there has been replacement
by less desirable species, such as carp and bullheads.
During the early decades of the neo-technical-urban phase (1900 to
present) the study area rivers continued to be subjected to the combined
influences of physical alteration and pollution. Between 1909 and 1910 a
decision to maintain a 9-foot channel throughout the length of the Ohio
River was made, and an additional 12 dams were constructed between Louis-
ville, Kentucky and Pittsburgh. The biota that is found in study area
rivers today must be viewed as the end product of cumulative impacts
associated with habitat modification—channelization, impounding, naviga-
tion channel maintenance, and siltation—coupled with impacts associated
with the discharge of petrusible and toxic wastes to these waters.
Starting around 1950, various activities contributed to improvement of
water quality in the upper Ohio River Basin. These included construction
of upstream dams on tributary streams which reduced seasonal flow maxima
and improved water quality. Municipal sewerage treatment plants have
increased in number and efficiency and industrial waste dischargers are now
95
-------
required to treat wastes prior to discharge. Acid mine drainage treatment
is somewhat alleviating acid and iron pollution problems, especially in the
Monongahela Basin.
The capacity for rivers in the study area to support a diverse and
abundant fish fauna is amply demonstrated by two studies in particular.
Krumholz and Minckley (1964) noted changes in the fish population of the
upper Ohio River following temporary pollution abatement subsequent to
closure of the steel industries on 15 July 1959. Collections of fishes
with rotenone from the auxiliary lock chamber at Montgomery Lock and Dam
(Ohio River Mile 31.7) yielded more than twice as many species and more
than five times as many individuals within 11 days after the beginning of
the steel strike than comparable samples taken from the same area before
the strike. They concluded that the principal difference in species
composition was the occurrence of "clean-water fishes" that invaded the
previously polluted area, probably from nearby unpolluted waters.
Fish population studies were conducted in the Monongahela River during
the period 1967-1973. The results of these studies were evaluated in
relation to trends in water quality. Comparative fish population statis-
tics obtained from the upper Monongahela River showed zero fish in 1967 and
8,071 fish in 1973 at the Maxwell Lock and Dam. The same type of data
obtained in the lower Monongahela River at Lock and Dam No. 2 revealed an
increase from 20 fish in 1967 to 869 fish in 1973. Improvements in the
fishery were attributed to improvement in water quality in the Monongahela
River (Preston 1974).
3.3 SPAWNING PERIODS FOR FISHES OF THE ALLEGHENY, MONONGAHELA, AND UPPER
OHIO RIVER
Hydropower development in the study area may result in biological
impacts through: (1) alteration of habitat required by indigenous fish
species for spawning; (2) alteration of current velocity profiles immedi-
ately downstream of dams and attendant scour and re-deposition of sediments
in transport to other portions of pools; (3) or alteration of dissolved
oxygen concentrations immediately downstream of dams as a result of the
reduction of reaeration occurring at dams retrofitted with turbines. The
96
-------
latter impacts would be most prominent on a temporal basis during the
period of lowest flow and highest temperature, generally between July and
September of each year. Therefore, before an assessment of the potential
for biological impacts associated with hydropower development can be under-
taken, the spawning period for the fishes of the study area must be
characterized as well as their habitat requirements. The habitat available
will be discussed, and this will be followed by a discussion of those
species which have been documented to spawn in the river.
A summary of the spawning period for species that occur in the upper
Ohio River and lower Allegheny and Monongahela Rivers was compiled from
Trautman (1981), Scott and Crossman (1973), Pflieger (1975), Smith (1979),
Lippson and Moran (1974), Lee et al. (1980), and several publications
dealing specifically with the life histories of select species (see Litera-
ture Cited). These data are presented in Figure 3-13, which depicts, on an
annual basis, the potential period of spawning for species that occur in
the study area. Several species (e.g., gizzard shad) have extended spawn-
ing periods. However, this reflects spawning throughout the entire
geographical range of this species. Spawning by this and other species in
the Ohio River Basin is confined primarily to the April to September
period, as will be discussed in a later section.
Populations of several species, including rainbow trout, brown trout,
muskellunge, and striped bass, are maintained through annual stocking by
various state agencies along the study area rivers or through downstream
migration into the Ohio River from its tributaries. For most species the
primary period of spawning is during spring or late spring and summer.
Study area fish that probably complete their spawning during the spring
include the lampreys, paddlefishes (if still present in the study area),
gars, bowfins, mooneyes, pikes, many suckers, killifishes, temperate
basses, perches, and sculpins. Spring and summer spawning species include
several of the minnows and carps, some suckers, freshwater catfishes,
sunfishes, and drums (Figure 3-13). The American eel is catadromous, a
marine spawning species. Information regarding spawning of a few other
species was not available.
97
-------
Spawning Period
Taxon
Jan Feb Mar Apr May Jun Jul Aug
Sep Oct Nov Dec
Peiromyzonndae - Lampreys
Ohio lamprey
Ichthyomyzon bdellium
iiiiimiiiii
Chestnut lamprey
Ichthyomyzon castaneus
iiiiiiiiiiiiniiiiiii
Stiver lamprey
Ichthyomyzon unicuspis
iiiiiiiiiiiiniiiiiii
Polyodontidae - Paddlefishes
Paddlefish
Polyodon spathula
iiiiiiiiiiiiniiiiiii
Lepisosteidae - Gars
Longnose gar
Lepisosteus osseus
iiiiiiiiiiiiiiniiiiiiiiiiii
Shortnose gar
Lepisosteus platostomus
iiiiiiiiiiiiniiiiiii
Amiidae - Bowftns
Bowfin
Amia calva
iiiiiiiiiiiiiiniiiiiiiiiiii
Anguillidae - Eels
American eel
Anguilla rostrata
Catadromous
Clupeidae • Herrings
Skipjack herring
Alosa chrysochloris
iiiiiimimiiiiim
Alewife
Alosa pseudoharengus
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiii
Gizzard shad
Dorosoma cepedianum
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiniiii
lllllllllllll
Hiodontidae - Mooneyes
Goldeye
Hiodon alosoides
iiiiiiiiiiiiniiiiiii
Mooneye
Hiodon lergisus
iiiiiiiiiiiiniiiiiii
Salmonidae ¦ Trouts
Rainbow trout
Salmo goirdneri
inn iiiiiiiiiiiiniiiiiii iiiiiii
lllll
Brown Irout
Salmo trutta
llllllillllilllllil
Esocidae ¦ Pikes
Redlm pickerel
Esox americanus
americanus
iiiiiiiiiiiiniiiiiii
Figure 3-13. The spawning period for the fishes occurring in the Allegheny,
Monongahela, and upper Ohio Rivers.
98
-------
Spawning Period
Taxon
Jan Feb Mar Apr May Jun
Jul Aug Sep Oct Nov Dec
Grass pickerel
Esox americanus
vermiculatus
Northern pike
Esox lucius
lllllllllllllllllllllllllll
IIIIIIIIIIIIII
lllllllllllllllllllll
Muskellunge
Esox masquinongy
llillllllllllllllllllllllll
Tiger Muskie
Hybrid - Non spawn
Cyprinidae - Minnows & Carps
Central stoneroller
Campostoma anomalum
iiiiiiiiiiiiiiiiiiiiiiimii
mil
Goldfish
Carasstus auratus
iiiiiiiiiiiiiiniiiiiiiiiiiiiiii
mini iiiiiiiiiiiii
Carp
Cyprinus carpio
iiiiiiiiiiiiiiiiiiiiniiiii
imimmi
Silverjaw minnow
Ericyrnba buccaia
iiiiiiiiiiiiiiiiiiiiiiiiiii
urn
Speckled chub
Hybopsis aestivalis
iniiiiiiiiiii
imimmi
Bigeye chub
Hybopsis amblops
iiiiiiiiiiiiiiiiiii
Streamline chub
Hybopsis dissimi/is
iiiiiiiiiiiii
Silver chub
Hybopsis sioreriana
iiiiiiiiiiiiiiiiiii
minium
River chub
Nocomis micropogon
IIIIIIIIIIIII
Golden shiner
Nolemigonus crysoleucas
iiiiiiiiiiiiiiiiiiiii
immmii
Popeye shiner
Noiropis anommus
Emerald shiner
Notropis atherinoides
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiii
River shiner
Notropis blennius
iiiiiiiiiiiniiiiiiiiiiii
Bigeye shiner
Notropis boops
iiiiiiiiiiiiii
mini
Ghost shiner
Notropis buchanani
mini
iiiiiiiiiiiii
Figure 3-13. (continued)
99
-------
Spawning Period
Taxon
Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec
Striped shiner
lllllilllllllllllllll
Notropis chrysocephalus
ItllllllllllVBIIIIIII
Common shiner
Notropis cornutus
lllllllllllllllllllllllllll
Blacknose shiner
Notropis heterolepis
Spottail shiner
IIIIIIIIIIIIIIIIIIIIIIIIIII
Notropis hudsomus
Silver shiner
No information on spawning season
Notropis photogems
Rosyface shiner
Notropis rubellus
lllllllllllllllllllllllllll
Spotfin shiner
Notropis spilopterus
lllllllllllll lllllll
Sand shiner
lllllllllllllllllllllllllll
Notropis strammeus
lllllllllllllllllllllllllll
Mimic shiner
Notropis volucellus
lllllilllllllllllllll
Steelcolor shiner
Notropis whipplei
lllllll lllllll
Suckermouth minnow
Phenacobtus mirabilis
lllllllllllllllllllllllllll
Bluntnose minnow
Pimpehales notatus
lllllllllllllllllllllllllll
Fathead minnow
Pimephales promelas
llllllllllllllllllllllllllll
Bullhead minnow
Pimephales vigilax
lllllilllllllllllllll
Blacknose dace
lllllilllllllllllllll
fthmichthys atratulus
lllllilllllllllllllll
Creek chub
Semotilus atromaculatus
lllllilllllllllllllll
Catostomidae • Suckers
River carpsucker
Carpiodes carpio
lllllll llllllllllllll
Quillback
llllllllllllllllllll
Carpiodes cyprmus
IlllllVIVIVIIIIVfllV
Highfm carpsucker
iiiiiiiiiiiiiiiiinii linn
Carpiodes veh/er
Figure 3-13. (continued)
100
-------
Spawning Period
Taxon
Jan Feb Mar Apr Mav Jun Jul Aug Sep Oct Nov Dec
White sucker
Catostomus commersoni
iiiiiiiiiimmiiiiiiimiiiiiiiimiii
Northern hog sucker
Hypentehum nigricans
iiiiiiiiiiiiiiiiiiiiiiinii
Smallmouth buffalo
Ictiobus bubalus
iiiiii iiiiiiiiiiiiii him
Bigmouth buffalo
Ictiobus cyprmellus
iiiiiiiiiiiiiiiiiiiii
Black buffalo
Ictiobus ntger
mini
Spotted sucker
Minytrema melanops
iiiiiiiiiiiiii
Silver redhorse
Moxostoma amsurum
iiiiiiiiiiiiii
River redhorse
Moxostoma carinatum
iiiiiiiiiiiiii
Black redhorse
Moxostoma duquesnei
iiiiiiiiiiiiii
Golden redhorse
Moxostoma erythrurum
iiiiiiiiiiiiiiiiiiiii
Shorthead redhorse
Moxostoma
macrolepidotum
llllllllllllllllllllllllllll
Ictaluridae - Catfishes
White catfish
Ictalurus catus
mini mini
Blue catfish
Ictalurus furcatus
niiiii mini
Black bullhead
Ictalurus melas
iimmiiiiiiiiiiiiiiiiiiiii
Yellow bullhead
Ictalurus natalis
iiiiiiiiiiiiii
Brown bullhead
Ictalurus nebutosus
mmiiiimimiiiimiii
Channel catfish
Ictalurus punctatus
iiiiiiiiiiiiiiiimiiiiiiimmiiiiiiiii
Mountain madtom
Noturus eleutherus
Figure 3-13. (continued)
101
-------
Spawning Period
Taxon
Jan Feb
Mar Apr May Jun Jul Aug Sep Oct Nov Dec
Stonecai
Noturus flavus
iiiiiimiiimiiimiiiiiiiiiiii
Tadpole madtom
Noturus gyrinus
iiiiiiiiiiiiiiiiiiiii
Brindled madtom
Noturus miurus
llllll llllllllllllll
Flathead catfish
Pylodictis ohvaris
iiiiiiiiiiiiii
Percopsidae - Trout-Perches
Trout-perch
Percopsts omiscomaycus
1
inn iimmmiiiiiiiiimiiiii
Cyprinodontidae - Ktllifishes
Banded killifish
Fundulus diaphanus
iiiiiimiimi
Blackstripe topminnow
Fundulus notatus
minimum mini
Atherimdae - Silversides
Brook silverside
Labidesthes sicculus
mini mini
Percichthyidae - Temperate
basses
White bass
Morone chrysops
II
iimiiiiiiiimimimi
Striped bass
Morone saxatihs
nun
miiiiimiiiiiiiiimiii
Centrarchidae - Sunfishes
Rock bass
Amblophtes rupestns
iiiiiiiiiiimimiuiiiii
Green sunfish
Lepomis cyanellus
mmmimmiii iiiiiiiiiini
Pumpkmseed
Lepomis gibbosus
iiiiiiiiiiiiiiiiiiiiiiiiiiii
Warmoutli
Leporms gulosus
iiiiiiiiiiiiii mini
Orangespotied sunfish
Lepomis humi/is
mini iiiiiiiiiiiiii
Bluegill
Lepomis macrochirus
iiiiiiiiiiiiii mimmmimim
Longear sunfish
Lepomis megatons
llllllllllllll lllllll
Figure 3-13. (cont
inued)
102
-------
Taxon
Spawning Period
Jan Feb Mar Apr May Jun Jul Aug Sep Oct Nov Dec
Redear sunfish
Lepomis microlophus
Smallmouth bass
Micropterus dolomieui
Spotted bass
Micropterus punctulatus
Largemouth bass
Micropterus salmoides
White crappie
Pomoxis annularis
Black crappie
Pomoxis nigromaculatus
Percidae • Perches
Greenside darter
Etheostoma blennioides
Rainbow darter
Etheostoma caeruleum
Fantail darter
Etheostoma llabellare
Johnny darter
Etheostoma nigrum
Orangethroat darter
Etheostoma spectabile
Banded darter
Etheostoma zonale
Yellow perch
Perca Havescens
Logperch
Percma caprodes
Channel darter
Percma copelandi
Blackside darter
Percma maculata
Sharpnose darter
Percma oxyrhyncha
Sauger
Stuostedion canadense
Walleye
Stuostedion vitreum
vitreum
llllllllllill llllllllllllll
iiiiiiiiiiiiii iiiiii
iiimmiiiiimtii
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiii
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiii
mini iiiiiiiiiiiiii
mmiiiiiiiiiiiiimimi
iiiiiiiiiiiiiiiiiiiiiiinii
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiinii
iiiiiiiiiiiiiiiiiiin
iiiiiiiiiiiiiiiiiiiii
iiiiiiiiiiiiiiiiiiiii
iiiiiiiiiiiiiiiiiiiiiiiiiiiiiiiini
iiiiii iniiiiiiiiiiiiiiiiiiiiiiiii
mini
iiiiiiiiiiiiiiiiiiiii
iimiiimiimiiimiimi
mmmmimiiiiiiiiiiiimiii
Figure 3-13. (continued)
103
-------
Spawning Period
Taxon Jan Feb Mar Apr May Jun J"1 A"9 Sep Oct Nov Dec
Sciaenidae - Drums
Freshwater drum
Aplodinotus grunniens
Cottidae ¦ Sculpins
Mottled sculpin
Cottus baifdi
iiiiii iiiiimmimimii
minium
Figure 3-13. (continued)
104
-------
The habitats available to Ohio River fishes for spawning was reviewed
by Pearson and Krumholz (1984). Macro-habitats available to fish include
the main channel, main channel border, shore-debris zone, tail waters, side
channels, sloughs and erabayments, creek mouths and flooded channels. They
described each of these as follows:
1. The main channel. This is the area of the river that is negoti-
ated by commercial barge traffic at normal pool elevation and is maintained
at least 9' deep and 300' wide by operations of the U.S. Army Corps of
Engineers. In most locations and at most seasons, it will be deeper and
considerably wider. A current of at least 0.5 ft/sec will always be
present. Severe scouring due to both high flows and the constant passing
of tow boats is a feature of this zone. The substratum is usually sand,
although gravel, rubble, and bedrock may be present. In some locations,
and at low water levels, silt and organic debris may also be found. Rooted
aquatic plants are absent.
2. Main channel border. This area of the river, between the main
channel and the shore-debris zone, is usually very narrow in the upper Ohio
River. The substratum is often sand or silt, although occasional extensive
deposits of gravel or rubble are found in the study area. Rooted aquatic
vegetation is absent, and sunken logs are rare.
3. The shore-debris zone. This zone extends from shoreline riverward
from 5 to 150 feet. It is characterized by the presence of dead trees
which are floating with the bole resting on the substrate or are rooted in
the substrate. The substrate is usually sand or silt, occasionally gravel,
with sunken logs and waterlogged branches widely scattered about and
partially buried in the bottom. Smaller pieces of vegetable matter often
accumulate on the larger pieces. Rooted aquatic vegetation (Potamogeton
spp.) is rare in the river, but when present it is found in bands 6-20 feet
wide in water 4-6 feet deep, and 15-50 feet offshore.
4. Tail waters. These areas are found extending 0.5 mile below each
navigation dam. They are characterized by having extensive turbulent
105
-------
areas, elevated oxygen concentration, and sand, gravel, or bedrock
substrates. No rooted aquatic vegetation is usually present.
5. Side channels. These areas usually separate near-shore islands
from the river's bank and contain running water at normal pool levels. In
the study area they are typically steep-sided, soft-bottomed, and are often
lined with eroded, slumping banks. Trees which have slumped into the
channel are also present.
6. Sloughs and embayments. These areas are connected to the river at
high water but may or may not have a narrow connection with the river at
normal water levels (sloughs do not, while embayments do). There is no
appreciable current through the area at normal water levels. These areas
often contain a great deal of standing and submerged timber, have soft
bottoms, and may have rooted aquatic vegetation.
7. Creek mouths and flooded channels. Construction of the navigation
dams resulted in the permanent flooding of many creek mouths. The habitat
resulting depends largely on the topography of the floodplain crossed by
the creek, the gradient of the creek near its mouth, and its mean dis-
charge. If the gradient is low the creek often forms a steep-banked,
soft-bottomed, canal of slack water extending from 600 to 3,000 feet up the
creek channel. The mouth is often blocked at low water by a silt bar. If
the gradient is higher the creek may maintain a noticeable flow and coarser
substratum almost to the mouth, and produce a gravel bar extending into the
main channel border.
3.A SPAWNING REQUIREMENTS AND REPRODUCTIVE GUILDS OF OHIO RIVER FISHES
The spawning requirements for each of the species recorded from the
study area are presented in Figure 3-14. These data are organized by the
most probable riverine habitat type used as a spawning site, substrate type
preferred, and fish nesting characteristics. As noted in a previous
section, several species have been extirpated, or greatly reduced in
abundance, in the upper Ohio River and near Pittsburgh; these include the
paddlefish, lake and shovelnose sturgeon, shortnose gar, bowfin, goldeye,
106
-------
Taxon
Spawning Preference
Habitat Type
Substrate
Type
Nesting Characteristics
Riverine
Mid-channel
Riverine
Marginal
Area
Tributaries
Pools
Riffles
Gravel
Vegetation
Unguarded
1 Guarded
Broadcast
None
Petromyzontidae - Lampreys
Ohio lamprey
•
•
•
•
Ichthyomyion bdellium
Chestnut lamprey
•
•
•
•
Ichthyomyzon castaneus
Silver lamprey
•
•
•
•
Ichthyomyzon unicuspis
Polyodonttdae - Paddlefishes
Paddleftsh
•
•
•
•
Polyodon spathula
Lepcsosteidae ¦ Gars
Longnose gar
•
•
•
•
•
Lepisosteus osseus
Shortnose gar
•
•
•
•
Lepisosteus platostomus
Amiidae - Bowfins
Bowfin
o
•
•
Amia calva
Anguillidae - Eels
American eel
Catadromous
Anguilla rostrata
Clupeidae • Herrings
Skipjack herring
•
9
A loss chrysochloris
Alewife
0
»
•
•
Alosa pseudoharengus
Gizzard shad
o
•
©
Dorosoma cepedianum
Hiodontidae ¦ Mooneyes
Goldeye
•
•
©
Hiodon alosoides
Mooneye
o
•
•
Hiodon tergisus
Salmonidae • Trouls
Rainbow trout
•
•
•
•
Solmo gairdneri
Brown trout
•
•
•
Salmo trutta
Figure 3-14. The spawning requirements for fish species occurring in the
Allegheny, Monongahela, and upper Ohio Rivers.
107
-------
Taxon
Spawning Preference
Habitai Type
a;
c
c
0) c
c r
z
s *
£ 5
o TO
c c
£ 5 <
o
o
a.
Substrate
Type
O
c
a
a>
>
Nesting Characteristics
3
CD
C
Z>
3
O
o
m
c
o
z
Esocidae - Pikes
Redfin pickerel
Esox americanus
americanus
Grass pickerel
Esox americanus
vermiculatus
Northern pike
Esox lucius
Muskellunge
Esox masqwnongy
Tiger Muskie
Cyprinidae ¦ Minnows & Carps
Central stoneroller
Camposloma anomalum
Goldfish
Carassius auratus
Carp
Cyprmus carpio
Silverjaw minnow
Encymba buccals
Speckled chub
Hybopsis aestivalis
Bigeye chub
Hybopsis amblops
Streamline chub
Hybopsis dissimilis
Silver chub
Hybopsis storeriana
River chub
Nocomis micropogon
Golden shiner
Noiemigonus crysoleucas
Popeye shiner
Notropis oriommus
o
O
Figure 3-14. (continued)
108
-------
Taxon
Emerald shiner
Notropis atherinoides
River shiner
Notropis blennius
Bigeye shiner
Notropis bo ops
Ghost shiner
Notropis buchanani
Striped shiner
Notropis chrysocephalus
Common shiner
Notropis cornutus
Blacknose shiner
Notropis heterolepis
Spottail shiner
Notropis hudsonius
Silver shiner
Notropis photogenis
Rosyface shiner
Notropis rubellus
Spotfm shiner
Notropis spilopterui
Sand shiner
Notropis strammeus
Mimic shiner
Notropis voiucellus
Steelcolor shiner
Notropis whipplei
SuCkermouth minnow
Phenacobius mirabilis
Bluntnose minnow
Pimephales notatus
Fathead minnow
Pimephales promelas
Spawning Preference
Habitat Type
ei m
c r.
£} Z 10
> (5 5
£ 5 <
Substrate
Type
O
u>
>
Nesting Characteristics
c
o
3
o
c
o
z
Figure 3-14. (continued)
109
-------
Spawning Preference
Habitat Type
Substrate
Type
Nes
ing Cha
ractens
lies
Taxon
Riverine
Mid-channel
Riverine
Marginal
Area
Tributaries
Pools
Riffles
Gravel
Vegetation
Unguarded
Guarded
j
Broadcast
None
Bullhead minnow
Pimephales vigilax
•
•
Blacknose dace
Rhinichthys alratulus
•
•
•
©
Creek chub
Semotilus alromaculatus
©
•
•
Catostomidae - Suckers
River carpsucker
Carpiodes carpio
•
•
Quillback
Carpiodes cyprinus
o
•
©
Highfin carpsucker
Carpiodes velifer
•
©
White sucker
Calostomus commersoni
•
•
•
•
•
©
«
Northern hog sucker
Hypentelium nigricans
©
©
©
•
•
•
Smallmouth buffalo
Ictiobus bubalus
©
•
•
Bigmouth buffalo
Ictiobus cyprinellus
e
•
©
•
©
•
Black buffalo
Ictiobus niger
•
•
•
•
•
Spotted sucker
Mmytrema melanops
©
•
Silver redhorse
Moxostoma amsurum
0
©
©
©
©
©
River redhorse
Moxostoma carinaturn
©
o
Black redhorse
Moxostoma duquesnei
o
©
©
•
©
Golden redhorse
Moxostoma nrythrurum
©
©
O
©
©
•
Shorthead redhorse
Moxostoma
macrolepidotum
•
•
•
o
•
>
©
Figure 3-14. (continued)
110
-------
Spawning Preference
Habitat Type
Substrate
Type
Nesting Character!
St'CS
Taxon
Riverine
Mid-channcI
Hiverine
Marginal
Area
Tributaries
Pools
{/>
O
<£
Gravel
Vegetation
"D
0)
•o
5
3
S>
C
D
Guarded
Broadcast
None
Ictaluridae ¦ Cathshes
White catfish
Ictalurus cat us
•
•
•
•
Blue catfish
Ictalurus furcatus
•
Black bullhead
Ictalurus melas
•
•
Yellow bullhead
Ictalurus natahs
Brown bullhead
Ictalurus nebulosus
•
•
•
•
•
•
Channel catfish
Ictalurus punctatus
•
•
•
•
•
•
Mountain madtom
Noturus eleutherus
•
•
•
Stonecat
Noturus flavus
•
Tadpole madtom
Noturus gyrinus
•
Brindled madtom
Noturus miurus
•
•
©
Flathead catfish
Pylodictis ohvaris
•
•
Percopsidae • Trout-Perches
Trout-perch
Percopsis omiscomaycus
©
•
•
Cyprmodontidae • Killifishes
Banded killifish
Fundulus diaphanus
Blackstripe topminnow
Fundulus notatus
o
e
©
©
©
Arherimdae - Silversides
Brook silverside
Lab/desthes sicculus
•
•
•
•
Percichthyidae - Temperate
basses
White bass
Morone chrysops
©
e
•
a
©
Figure 3-14. (continued)
111
-------
Spawning Preference
Habitat Type
Substrate
Type
Nesting Ch<
iracteri;
>tics
Taxon
o
c
u
>
(£
Mid-channel
Riverine
Marginal
Area
Tributaries
Pools
Riffles
Gravel
Vegetation
Unguarded
Guarded
Broadcast
None
Striped bass
Morone saxatihs
Centrarchidae - Sunfishes
Rock bass
Amblophtes rupestris
©
©
•
Green sunfish
Lepomis cyanellus
•
•
Pumpkinseed
Lepomis gibbosus
•
•
•
Warmouth
Lepomis gulosus
•
•
Orangespotted sunfish
Lepomis humilis
•
Bluegill
Lepomis macrochirus
•
•
Longear sunfish
Lepomis megalolis
•
•
•
•
Redear sunfish
Lepomis microlophus
•
o
•
Smallmouth bass
Micropterus dolomieui
•
•
•
o
©
Spoiled bass
Micropterus punctulatus
•
Largemonlh liass
Micropterus sahnoides
•
•
©
Whne crappie
Pomoxis annularis
©
©
9
Black crappie
Pomoxis nigromaculatus
©
©
Percidae • Perches
Greenside darter
Etheostoma blennioides
•
o
©
©
Rainbow darter
Etheostoma caeruleum
©
©
©
Fantail darter
Etheostoma /label/are
©
©
©
©
Figure 3-14. (continued)
11?
-------
Taxon
Johnny darter
Etheostoma nigrum
Orangethroat darter
Etheostoma spectabile
Banded darter
Etheostoma ronale
Yellow perch
Perca flavescens
Logperch
Percina caprodes
Channel darter
Percina copelandi
Blackside darter
Percina maculate
Sharpnose darter
Percina oxyrhyncha
Saug er
Stuostedion canadense
Walleye
Stuostedion vitreum
vitreum
Sciaenidae ¦ Drums
Freshwater drum
Aplodmotus grunniens
Cottidae - Sculpins
Mottled sculpin
Coitus bairdi
Spawning Preference
Habitat Type
c
c
01 Q
c z.
r o
S "5
£ 5
a) n
c c
5 ? *
> • •
(E 5 <
3
¦O
O
o
Q.
Substrate
Type
o
o>
>
Nesting Characteristics
c
3
3
o
D
C
o
z
Figure 3-14. (continued)
113
-------
gizzard shad, smallmouth and highfin buffaloes, river carpsucker, blue
sucker, sturgeon sucker, river shiner, silvery minnow, blue catfish,
American eel, sauger, and freshwater drum (Lachner 1956). Other species
only rarely captured include the Ohio lamprey, shorthead redhorse, spotted
sucker, flathead catfish, slenderhead darter, and warmouth. Spawning
requirements for sturgeon, blue sucker, sturgeon sucker, silvery minnow,
and slenderhead darter were omitted from Figure 3-14 because lack of recent
records and/or improbability of these species becoming re-established in
the fishery.
Balon (1975) devised an ecological means of classifying fishes based
upon their reproductive behaviors, preferred spawning substrates, and
morphological adaptation of the eggs and larvae. Balon's classification
scheme provides a framework upon which the known information on spawning
habits of Ohio River fish can be arranged and evaluated with regard to
availability of habitat. Balon's scheme begins with the premise that two
environmental factors are primary determinants of survival during the
critical embryological and larval development of fishes: predators and the
availability of oxygen.
The fishes of the Ohio River have, therefore, two primary objectives
in spawning: (1) to deposit their fertilized eggs where predators cannot
destroy them; and (2) to deposit them where they will not be deprived of
oxygen due to siltation, lack of current, or bacterial respiration (Pearson
and Kruraholz 1984).
Pearson and Krumholz (1984) attempted to fit each of the species of
fishes reported from the Ohio River into Balon's classification (Table
3-11). Of the 154 species of fishes reported from the mainstem of the Ohio
River, the American eel was eliminated from consideration because it spawns
in the ocean, and nine introduced species were ignored which have not
established reproducing populations. Of the remaining 144 species,
inadequate descriptions of the reproductive habits of 18 species were
available to permit their assignment to a guild. The 126 species which
were assigned to reproductive guilds are listed in Table 3-11 (from Pearson
and Kruraholz 1984).
114
-------
Table 3-11. Reproductive guilds of the 126 species of fish which repro-
duced in the Ohio River, and for which information on spawning
habits is available (after Balon 1975). Numbers in ( ) indi-
cate numbers of species within each group. Definitions of the
terras are provided in the text.3
Balon's (1975) Subsections
Ohio River Fishes
A. NONGUARDERS
A.l Open substrate spawners
A. 1.1 Pelagophils (2)
A.1.2 Litho-pelagophils (5)
A.1.3 Lithophils (28)
A.1.4 Phyto-lithophils (14)
Notropis atherinoides
Aplodinotus grunniens
Acipenser fulvescens
Dorosotna cepedianum
Hiodon (2)
Lota lota
Scaphirhynchus platorynchus
Polyodon spathula
Alosa (2)
Clinostomus elongatus
Hybopsis aestivalis
Notropis (3)
Phenacobius mlrabilis
Phoxlnus erythrogaster
Rhinichthys atratulus
Catostomids (12)
Percopsis omiscomaycus
Stizostedion (2)b
Cottus carolinae
Dorosoma petenense
Hybognathus nuchalis
Hybopsis (2)
Notropis (3)
Carpiodes carpio
Ictiobus bubalus
Fundulus notatus
Labidesthes sicculus
Morone (2)
Perca flavescens
A.1.5 Phytophils (17)
Lepisosteus (4)
Esox (3)
Carassius auratus
Cyprlnus carpio
Notemigonus crysoleucas
Notropis (3)
Erimyzon sucetta
Ictiobus (2)
Fundulus dlaphanus
115
-------
Table 3-11. (continued)
Ohio River Fishes
Ericymba buccata
Notropis (3)
Carpiodes cyprinus
Ammocrypta asprella
Percina caprodes
Lampreys (5)
Nocomis (2)
Semotilus atromaculatus
Etheostoma caeruleum
Percina (4)
Pomoxis annularis
Campostoma anomalum
Notropis (4)
Ictalurus melas
Centrarchids (10)
Amia calva
Centrarchids (2)
Etheostoma (2)
B.2.5 Speleophils (16) Pimephales (3)
Ictalurids (9)
Etheostoma (4)
B.2.6 Polyphils (1) Lepomis gibbosus
C. BEARERS
C.2 Internal
C.2.3 Viviparous (1) Gambusia affinis
aFrom Pearson and Krumholz 1984.
^Recent and convincing evidence indicates that the walleye and sauger
belong in the A.1.2, litho-pelagophil guild. (McElman, J.F. 1983.
Comparative embryonic ecomorphology and the reproductive guild classifica-
tions of walleye, Stizostedion vitreum, white sucker Catostomus
commersoni. Copeia 1983(1) :256-260).
Balon's (1975) Subsections
A.1.6 Psamraophils (7)
A.2 Brood hiders
A.2.1 Lithophils (13)
B. GUARDERS
B.l Substratum choosers
B.1.2 Phytophils (1)
B.2 Nest spawners
B.2.1 Lithophils (16)
B.2.2 Phytophils (5)
116
-------
Balon proposed 32 reproductive guilds divided into three major
sections, each with two subsections: (1) nonguarders, which ignore eggs
and larvae after spawning and either spawn on open substrates or hide their
broods; (2) guarders, which protect and/or aerate eggs and larvae after
spawning and either choose the substrate on which the brood is reared, or
construct a nest to receive the brood; and (3) bearers, which carry their
eggs either on or in the parent's body. Nearly 70 percent of the fishes in
the Ohio River (86 species) were placed in the "nonguarders" section (Table
3-11), while 29 percent were placed in the "guarders" section (38 species),
and only one species (mosquitofish) was placed in the "bearers" section.
Thirteen of Balon's 32 guilds were represented in the Ohio River fish
community (Pearson and Krumholz 1984).
Three of the most abundant fishes found in fisheries studies in the
upper Ohio River Basin in recent years, the emerald shiner, gizzard shad,
and freshwater drum, are either pelagophils (A.1.1) or litho-pelagophils
(A.1.2). The eggs and/or larvae of pelagophils and litho-pelagophils are
buoyant or semi-buoyant, are adapted to highly oxygenated waters, and have
no or poorly-formed embryonic respiratory organs. Apparently, producing
pelagic or semi-pelagic eggs and/or larvae has been a most successful
strategy in the Ohio River for these three species (Pearson and Krumholz
1984). Four other litho-pelagophils in the Ohio River are today either
extirpated (lake sturgeon), rare (burbot), or low in abundance (goldeye and
mooneye).
Slightly more than 22 percent of the fishes in the Ohio River (28
species) were considered to be non-guarding lithophils and make up the
largest single reproductive guild. Lithophils (A.1.3) deposit their eggs
over clean gravel-rock substrates, the larvae are photophobic, and they are
adapted for living in well-oxygenated interstitial waters. The embryonic
respiratory system is only moderately developed in these fishes.
Representative fishes of this guild include redhorses, white sucker, blue
sucker, sauger, paddlefish, shovelnose sturgeon, and several minnows (Table
3-11). It seems likely that the overall reproductive success of this guild
has declined with canalization and siltation of the Ohio River and its
tributaries in the last 80-100 years (Pearson and Krumholz 1984).
117
-------
The non-guarding phyto-lithophil (A.1.4) guild of fish contains 14
Ohio River species. This guild represents an intermediary group midway
between the reproductive modes of the lithophils and the nonguarding
phytophils (A.1.5). The phytophils deposit their eggs over either live or
dead vegetation, flooded plants, and vegetable debris. The larvae typi-
cally are not photophobic, have cement glands on the head to attach them-
selves to vegetation off the soft bottom, and have highly developed
embryonic respiratory structures which adapt them for survival in poorly-
oxygenated situations. Seventeen species of Ohio River fishes belong to
the phytophil guild. Two members of these two guilds were represented
among the most abundant species found in the upper Ohio River: the mimic
shiner (phyto-lithophils) and common carp (phytophil). Some other typical
and common members of these two guilds include the buffalofishes, river
carpsucker, silvery minnow, silver chub, and white bass. It seems likely
that the relative reproductive success of members of these two guilds would
have increased following canalization and siltation of the Ohio River
(Pearson and Krumholz 1984).
The non-guarding psammophils (A.1.6) were represented by just seven
species, of which only the sand shiner is very abundant. These fishes
spawn over clean, coarse sand substrates. The non-guarding brood hiders
(lithophils A.2.1) were represented by 13 species, but none of them are
very abundant in the river (Table 3-11).
Members of the "guarder" guilds remain near their spawn and are able
to offer protection against predators and provide artificial aeration by
cleaning and fanning the eggs. With this strategy fishes are able to
reproduce in situations where fine sediments and low oxygen concentrations
would otherwise be prohibitive.
The white crappie represents the only Ohio River fish of the guarder-
substratum chooser-phytophil (B.1.2) guild. This species spawns over
vegetation, fine roots, or vegetable debris. The spawning site is cleaned
and ^guarded, and the newly-hatched larvae swim constantly to avoid the
hypoxic substrate beneath the cleaned vegetation.
118
-------
AH of the other guarders in the Ohio River (23 species) are nest
spawners, that is, they actually construct a cleaned depression on the
substratum or clean a naturally-occurring cavity or crevice, where the eggs
are deposited. The nest-spawning lithophils (B.2.1; 16 species) include 10
of the 12 centrarchids in the river, five uncommon minnows, and the black
bullhead. The larvae of most fishes in this group hide in the gravel at
the bottom of the river, may have cement glands, and their embryonic
respiratory organs are moderately- to well-developed. Included in this
guild are the spotted and smallmouth basses, bluegill, green sunfish, and
longear sunfish. Many of the species in this group prefer to spawn in
relatively still backwaters, which are not abundant along the Ohio River.
The nest-spawning phytophil (B.2.2) guild includes just five Ohio
River species: the bowfin, two darters, and two centrarchids—the large-
mouth bass and black crappie. The bowfin and the centrarchids also prefer
to nest in the relatively still backwaters. It is possible that one reason
these fishes are not abundant in the mainstem area is that they do not nest'
successfully in shallow areas which are constantly disturbed by tow boat
wakes.
The nest-spawning speleophil (B.2.5) guild includes 16 species of Ohio
River fishes: the three Pimephales minnows, nine catfish, and four darters
(Table 3-11). These fishes guard their eggs after depositing them on the
underside of an object or in a natural cavity. The eggs and larvae are
fanned by the parents, and consequently, oxygen supply is seldom a problem.
The brown bullhead and channel catfish are two members of this successful
guild. The pumpkinseed, a relatively uncommon fish of the upper Ohio
River, is considered to be a polyphil (B.2.6) because it spawns on nearly
any substrate type.
3.5 LARVAL AND JUVENILE FISHES IN THE DRIFT OF THE OHIO, ALLEGHENY, AND
MONONGAHELA RIVERS
The previous two sections of this chapter have characterized the
fisheries resources of the study area and the spawning requirements of each
species. This section will characterize the occurrence of fish eggs and
larvae (ichthyoplankton) in the drift of study area rivers. Most data
119
-------
available regarding the occurrence of ichthyoplankton at various sites
along the rivers results from information compiled and presented in
fulfillment of the mandates stipulated in the National Environmental Policy
Act (NEPA) of 1969 and PL 92-500 of 1972, especially subsections 316(b) of
the latter. Electrical utilities located in the upper Ohio River Basin
have complied with NEPA and PL 92-500 by monitoring ichthyoplankton in the
rivers or by monitoring ichthyoplankton entrained,in cooling water passing
through generating facilities.
The discussion of larval and juvenile fishes includes data from
outside the study area, for comparatively little information was available
for the Allegheny and Monongahela Rivers. Considerably more information
was available for the upper 260 miles of the Ohio River. Therefore, a
compilation of the taxa occurring in the ichthyoplankton of the upper Ohio
River (RM 0-260) is included. However, characterization of the relative
abundance and absolute density of ichthyoplankton will center on long-term
monitoring that has been conducted at Ohio River Mile 53.9, in the New
Cumberland Pool, and at Ohio River Mile 76.7, in the Pike Island Pool.
Monitoring at these two sites has been conducted from 1976 through 1982 and
from 1978 through 1982, respectively (WAPORA, Inc. 1980, Geo-Marine, Inc.
1981, 1982).
Figure 3-15 presents an overview of the taxa that have been identified
in ichthyoplankton samples collected from the upper Ohio River Basin.
These include the following families of fishes: Clupeidae, Hiodontidae,
Umbridae, Cyprinidae, Catostomidae, Ictaluridae, Cyprinodontidae, Atherini-
dae, Percopsidae, Percichthyidae, Centrarchidae, Percidae, and Sciaenidae.
Taxa within the table that have been identified to species represent
advanced larval stages or juveniles, both of which have morphological
characteristics developed to the point that species determinations can be
made. Taxa identified only to the generic or some higher level generally
represent larvae in very early stages of development, i.e., prolarvae, for
which determination to species level cannot be made with certainty. From
the standpoint of taxonomic composition, the Cyprinidae, Catostomidae,
Centrarchidae, and Percidae have the greatest number of taxa represented in
ichthyoplankton collections (a total of 59 taxa).
120
-------
Clupeidae
Dorosoma spp or Alosa spp
A. chrysochloris
Dorosoma spp
D. cepedianum
Hiodontidae
Hiodon spp
H. tergisus
Umbridae
Umbra limi
Cyprimdae
Cyprmus carpio ¦ Carassius auratus
C. carpio
Hybopsis spp.
H storeriana
Notemigonus cryso/eucss
Notropis spp.
N. atherinoides
N blennius
N hudsomus
N rubellus
N. spilopterus
N. strammeus
N. voluce/lus
Pimephales spp
P. notatus
P. vigitax
Rhinichthys atratulus
Semotilus atromaculalus
Caiostomidae
Carpiodes spp. or Iciiobus spp.
Carpiodes spp.
C. carpio
C. cyprinus
Catostomus commersoni
C yclept us elongatus
Hypentelium nigricans
Iciiobus spp
/ bubalus
Mmytrema melanops
Moxostoma spp
ictaluridae
Ictalurus spp.
/. natahs
I. punctatus
Pylodictis olivaris
Noturus spp
N llavus
April
May
June
July
August
September
Figure 3-15. The temporal distribution of fish larvae and juveniles in.the
drift in the Allegheny, Monongahela, and upper Ohio Rivers.
121
-------
Percopstdae
Percopsis omiscomaycus
Cyprinodontidae
Fundulus spp
Atherinidae
Labidesthes sicculus
Percichihyidae
Morone spp.
M. chrysops
Centrarchidae
Amblophtes rupestris
Lepomis spp. ¦ Pomoxis spp
Lepomis spp.
L. cyanellus
L macrochirus
Micropterus spp
M. dolomieui
M punctulatus
M. salmoides
Pomoxis spp
P. annularis
P mgromaculatus
Percidae
Etheostomatinae
Etheostoma spp
E. b/ennioides
E caeruleum
E. nigrum
E variatum
E zonale
Perca flavescens
Percina spp.
P caprodes
P. shumardi
Stizosledion spp
S. canadense
S vitreum
Sciaemdae
Aplodmotus grunniens
April
May
June
July
August
September
Figure 3-15. (continued)
122
-------
The seasonal occurrence of each taxon in the ichthyoplankton is
presented in Figure 3-15. This summary is probably inclusive of the
spawning period for the majority of species that reproduce in the study
area, however, some species are known to spawn during other seasons and
would not be represented (Figure 3-13). The majority of ichthyoplankton
sampling conducted at the various sites has been conducted from mid- to
late-April through August. The spawning season is usually initiated in mid
to late April and continues into August. However, the latter part of May,
June, and early July is the period of spawning activity by the greatest
number of species. Ichthyoplankton densities are typically low during
April and early May, peak during June or July, and decrease again in
August, as the following discussion will illustrate.
Ohio River
Figures 3-16 through 3-19 present an overview of the ichthyoplankton
density and species composition that occurs in the New Cumberland and Pike
Island Pools of the upper Ohio River. Data presented in Figures 3-16 and
3-17 represent sampling that was conducted in the New Cumberland Pool
between 1976 and 1982, whereas Figures 3-18 and 3-19 cover sampling between
1978 and 1982 in the Pike Island Pool. Results from 1976-1980 represent
the composite of weighted means of day and night tows with 0.5 meter
diameter ichthyoplankton nets (WAPORA, Inc. 1977-1981); 1981 and 1982 data
are the results from nighttime tows with 1.0 meter diameter nets
(Geo-Marine, Inc. 1982, 1983).
In the New Cumberland and Pike Island Pools, peaks in ichthyoplankton
density have occurred in June, July, and August, and May, June, July, and
August, respectively. The temporal occurrence of the peak depends upon
which species numerically dominate the spawn (Figures 3-16 and 3-18). In
the New Cumberland Pool, species numerically dominating the ichthyoplankton
during April include the perches, suckers, and minnows and carps; during
May the previous three groups continue to dominate the ichthyoplankton
assemblage; by June the percids typically decrease in abundance and minnows
and carps, suckers, herrings, and "others" numerically dominate; minnows
and carp, herrings, drums, and "others" dominate in July and August (Figure
123
-------
2.0
1.5
1.0
.5
5.00
4.50
2.50
2.00
1.50
1.00
.50
15
10
5
15
10
5
10
5
10
5
10
5
0
ire 3
1976
v = < 1 /10M3
~ = 0
i i i p.? w q pip
* m * Vt TX « PI P.
1978
J_J I L
i i *i Pi Pi Pi P! PI
1979
' Q-*—°' ' ' '
?/TNp.
1981
J IT IP IP IV IP IPXl ^U7 IP*! fr ¦ I P I I I
V |V| 7i7i7
7 14 21 285 12 1926 2 9 16 2330 7 142128 4 1118 25 1 8 1522 29
APRIL MAY JUNE JULY AUGUST SEPTEMBER
6. Density of ichthyoplankton collected weekly in net tows near
the New Cumberland Pool, 1976-1982.
124
-------
Q HERRINGS ^FRESHWATER CATFISHESQ DRUMS QpERCHES
[^jsUNFISHES ^MINNOWS AND CARPS QSUCKERS | jOTHER
100
90
80
70
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Figure 3-17. Weekly percent composition of all tow samples by dominant families (>10%)
near the New Cumberland Pool, 1976-1982.
-------
Q HERRINGS |i] FRESHWATER CATFISHEsI | DRUMS
[~]SUNPISHES ^MINNOWS AND CARPS [ ] SUCKER
100
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70
60
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Figure 3-17. (continued)
| [other
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(V O)
-------
v =< .1/10m3
6
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JUNE JULY AUGUST SEPT
Figure 3-18. Density of ichthyoplankton collected weekly in net tows near
the Pike Island Pool, 1978-1982.
127
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t: < ,1/10m3
»= 0
1981
4
2
0
1982
8
6
4
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APRIL MAY JUNE JULY AUGUST SEPT
Figure 3-18. (continued)
128
-------
Q HERRINGS ^ FRESHWATER CATFISHES ~ DRUMS QpERCHES
||3suNFISHES ^MINNOWS AND CARPS SUCKERS | |OTHER
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Figure 3-19. Weekly percent composition of all tow samples by dominant
families (>10%) near the Pike Island Pool, 1978-1982.
129
-------
3-17). A similar temporal sequence in species numerically dominating the
ichthyoplankton occurs in the Pike Island Pool (Figure 3-18), and at other
locations in the upper Ohio River Basin. Exceptions occur, but they
reflect the differences that are present in the composition of the fishery
at a location rather than the period over which a particular species will
spawn. Families of fishes that have many species represented in the
community typically have extended spawning periods as not all species spawn
simultaneously. Differences in the initiation of spawning during a
particular year for a given taxon, i.e., perches in Figures 3-16 and 3-18,
may be accounted for by differences in river flow among years and/or
differences in the onset of warming of river waters.
Entrainment sampling conducted on three dates in June 1976 at the
Bruce Mansfield Power Plant (Ohio River Mile 33.7) resulted in the collec-
tion of only fish eggs. The average density during this period was 139
eggs/100 (Pennsylvania Power Company 1976). Similarly, entrainment
sampling during April, May, and June at the Shippingport Atomic Power
Station (Ohio River Mile 35.0) yielded no fish eggs and only one cyprinid
larvae (Equitable Environmental Health, Inc. 1979).
Ichthyoplankton monitoring in the Ohio River near the Beaver Valley
Power Station (River Mile 34.9) from April through July 1976 and 1978
resulted in the collection of 18 taxa distributed among the Clupeidae,
Cyprinidae, Catostomidae, Centrarchidae, Percidae, and Sciaenidae.
Walleye-sauger and yellow perch larvae were the first taxa in the drift in
April and May. By late May, gizzard shad, minnow, crappie, and darter
larvae were present. Gizzard shad and minnow and carp larvae numerically
dominated collections during June and July each year (NUS Corporation 1976;
Duquesne Light Company 1979).
Twelve entrainment collections were made from March 2 to Augut 21,
1978 at the Frank R. Phillips Power Station (Ohio River Mile 15.2). Only
19 larvae and no fish eggs were collected. No eggs or larvae were collec-
ted from March 2 to May 4; larvae were collected each biweekly sampling
period from May 25 through July 20, and again on August 21. Of the larvae
collected, seven were unidentifiable due to mechanical damage. Of the
130
-------
remaining larvae, 11 were cyprinids (probably Notropis spp.) and one was a
clupeid (herring). With so few specimens to compare, identification to
family was deemed the most accurate. The greatest number of larvae
collected over a 24-hour sampling period was nine on June 8 (average
density = 13.7/100 m3) (Equitable Environmental Health, Inc. 1979).
Monongahela River
Entrainment sampling was conducted at the Mitchell Power Station,
located at Monongahela River Mile 29.4, from April 1981 through March 1982.
Ichthyoplankton was sampled once every two weeks during the period 15 April
through August 1981 and once a month from September 1981 through March
1982. This sampling yielded a total of 3 eggs, 552 larvae, 27 juveniles,
and 3 adults of 12 taxa. The taxa collected included the following:
gizzard shad, common carp, emerald shiner, mimic shiner, shiners (unidenti-
fiable), bluntnose minnow, minnow (unidentifiable), channel catfish,
bullheads (unidentifiable), sunfish (unidentifiable), bass (unidentifi-
able), darter (unidentifiable), walleye or sauger, and freshwater drum.
Larvae were present in samples collected from April through September,
but were most abundant on 22-23 July (56.00/100 m3), 8-9 July (25.27/100
m3) , and 24-25 June (14.50/100 m3). Juveniles were collected during
four sampling dates, 5-6 August (1.51/100 m3), 19-20 August (131/100
m3), 16-17 September (0.38/100 m3) , and 20-21 January (0.73/100 m3).
Adults were taken during two sampling dates 24-25 June (0.18/100 m3) and
17-18 March (0.32/100 m3).
Larval catch was dominated by gizzard shad (mean yearly density =
2.61/100 m3; 35.9% of the total catch), minnow (1.79/100 m3; 25.4%),
common carp (0.26/100 m3; 3.8%), emerald shiner (0.16/100 m3; 2.4%),
and channel catfish (0.12/100 m3; 1.4%). Unidentifiable specimens repre-
sented 28.1% of the total annual catch (mean = 2.05/100 m3). Juvenile
specimens were dominated by gizzard shad, emerald shiner, and shiners each
comprising 22.2% of the total catch (mean = 0.07/100 m3). Bluntnose
minnow (mean =» 0.05/100 m3), mimic shiner (0.02/100 ra3), minnow
(0.01/100 m3), and channel catfish (0.01/100 m3) were the remaining
131
-------
juveniles collected. Most juveniles (70.4%) were taken during the 5-6 and
19-20 August sampling surveys. Two emerald shiners and one bluntnose
minnow comprised the adult specimens taken during the sampling year (NUS
Corporation 1982).
An evaluation of entrainment at the Hatfield Ferry Power Station
(Monongahela River Mile 78.9) was conducted during 1979 (Energy Impact
Assoc., Inc. 1980). A total of 18 one-hour periods were sampled on three
occasions from May through July. No fish eggs or larvae were collected
during this sampling.
Entrainment sampling was conducted twice monthly from September
through November 1977 and May through September 1977 at the Elrama Power
Station (Monongahela River Mile 25.0). Six families of fish—Clupeidae,
Cyprinidae, Catostomidae, Ictaluridae, Centrarchidae, and Percidae—were
represented in the entrainment samples. Minnows were the most abundant
group, and the clupeids (i.e., gizzard shad) were also abundant. Fifteen
species of larvae were identified, but most specimens could not be identi-
fied below the family level.
Fish eggs and larvae were present primarily from early June to early
August 1978, but a few specimens were collected in late April and May and
late August and early September 1978. The peak density (99/100 m^) of
eggs and larvae occurred during 28-29 June 1978. The first specimens to
appear in the samples were walleye in late April and early May. A mixture
of percids (yellow perch and darters) and minnows appeared in late May. In
June, minnows, including carp and emerald shiner, and gizzard shad began to
dominate the samples. Few specimens were entrained after early August
(Ecological Analysts, Inc. 1978).
Allegheny River
During sampling for preparation of a 316(b) demonstration for the
Armstrong Power Station (Allegheny River Mile 55.4), ichthyoplankton was
sampled between November 1976 and September 1977. Monthly entrainment
samples were collected from November through March and again in July,
132
-------
August, and September. Weekly samples were collected from early April
through mid-June. During the 57 one-hour samples, 116 larval and juvenile
fish and one fish egg were collected. Larval and juvenile minnows (blunt-
nose minnow, emerald shiner, mimic shiner, and unidentifiable cyprinids)
were the most frequently encountered group (62.1% of the total), followed
by larval perch (Johnny darter and unidentifiable perch and darter)
(16.4%), and unidentifiable larvae (12.1%). Other taxa collected included
the following: spotted sucker (0.8%), unidentifiable sucker (2.6%),
unidentifiable sunfish (1.7%), and unidentifiable catfish (1.7%) (Energy
Impact Assoc., Inc. 1978).
The number of larval and juvenile fish collected during each sampling
period varied seasonally, with entrainment densities ranging from 0/100 to
105.77/100 m^. Highest numbers of larval and juvenile fish were obtained
in June and July when monthly densities averaged 103.04 and 84.14/100
respectively. Minnows and darters were most abundant at these times.
3.6 DISSOLVED OXYGEN AND ITS INFLUENCE ON FISHES
A possible constraint to the development of hydropower at existing
dams in the study area is the potential for depression of dissolved oxygen
concentrations. Currently, water passing over dams contributes substan-
tially to reaeration of waters of the study area rivers, and results in a
zone of comparatively high dissolved oxygen at the downstream face of dams.
Passage of water through turbines installed in dams may circumvent reaera-
tion and may result in a dissolved oxygen sag in a downstream direction.
This could cause adverse impacts on fishery resources.
This portion of the literature review will focus on impacts of reduced
dissolved oxygen on the fishery. The general consequences of depressed
dissolved oxygen concentrations on fish, and more specifically, the levels
at which biological impacts could be expected to occur are summarized.
This information, when combined with the results of water quality modeling,
will, enable evaluation of the impacts associated with hydropower develop-
ment in the study area.
133
-------
Aerobic organisms utilize the process of diffusion to move dissolved
oxygen into their systems by means of an internal-external oxygen pressure
gradient. The exchange process is often facilitated by a delivery system
(e.g., branchial and opercular pumps in fish) and a transport system (e.g.,
internal circulatory system) to distribute oxygen within the body. In all
aerobic organisms, movement of oxygen to the tissues for metabolism is
fundamentally via tension gradients, both inside and out of the body. The
oxygen tension gradient between tissues and the external medium is thus
critical to the gas exchange process (Davis 1975). Relationships have been
established between oxygen consumption of fish and water temperature, water
dissolved oxygen content, water carbon dioxide level, size of fish, activ-
ity, photoperiod, and other variables (Andrews and Matsuda 1975). Recent
comprehensive reviews of the dissolved oxygen requirements of fish have
been prepared by Doudoroff and Shumway (1970), Warren et al. (1973), and
Davis (1975) and much of the following overview is derived from these
sources.
Reduction in the level of available oxygen affects physiological,
biochemical, and behavioral processes in fish. Restrictions in the supply
of oxygen available for metabolic processes including swimming, migrating,
and feeding are caused by hypoxia (Davis 1975). Katz et al. (1959) evalu-
ated the ability of salmon and largeraouth bass to swim in water with
reduced oxygen content. Largemouth bass were found to display marked
seasonal changes in ability to swim at reduced oxygen concentrations.
During September, bass were able to swim against a current of 0.8 feet per
second (fps) for one day at 25°C in water having a mean dissolved oxygen
content of 2.0 mg/1. In early December, at temperatures of 15.5 to 17.0°C,
bass could swim against an 0.8 fps current when the water was nearly
saturated, but were unable to do so by the time the oxygen level was
reduced to 5.0 mg/1. Salmon swimming was impaired at low dissolved oxygen
concentrations, a factor that could be important to this migratory species
(Katz et al. 1959). Reduction in feeding at reduced dissolved oxygen
concentrations has been observed in channel catfish, yellow perch, northern
pike, largemouth bass, bluegill, and walleye (Raible 1975, Petit 1973).
134
-------
Developing fish eggs and larvae show a number of responses to low
oxygen including respiratory dependence, retarded growth, reduced yolk sac
absorption, developmental deformities, and mortality (Davis 1975, Doudoroff
and Shumway 1970). Laboratory studies evaluating the response of
warm-water fish species to low dissolved oxygen have been conducted for the
following species: white sucker (Siefert and Spoor 1974, Oseid and Smith
1971a), largemouth bass (Dudley and Eipper 1975; Spoor 1977; Carlson and
Siefert 1974), walleye (Siefert and Spoor 1974, Oseid and Smith 1971b),
black crappie (Siefert and Herman 1977), common carp (Kaur and Toor 1978),
channel catfish (Carlson et al. 1980), yellow perch (Carlson et al. 1980),
northern pike (Siefert et al. 1973, Adelman and Smith 1970), smallmouth
bass (Siefert et al. 1974), and white bass (Siefert et al. 1974). The
results of these studies are tabulated in Table 3-12.
Avoidance behavior has been reported for some species in response to
low oxygen, although reports of dissolved oxygen thresholds to initiate
this behavior vary considerably (Davis 1975). Observed behavior patterns
in low O2 include increased activity, altered phototaxis, and air gulp-
ing. Whitmore et al. (1960) demonstrated avoidance of waters containing
1.5 mg/1 by largemouth bass and bluegill, and Hill (1969) reported that the
American eel consistently selected high over low oxygenated water; the
tolerance point for oxygen selection was near 2.5 mg/1 at 21°C. The
air-water interface may provide a partial means for fish to avoid hypoxia
in the underlying water column. The high cost of maintaining aerobiosis in
hypoxic water or the lower energy yield of switching to anaerobic metabo-
lism are thus avoided. Not only do the top few millimeters or centimeters
of severely hypoxic or even anoxic natural bodies of water have an apprec-
iable oxygen content, but the air itself may also be potentially important
as a direct source of oxygen for fish (i.e., "air-gulping" in goldfish)
(Burggen 1982). During oxygen depletion, the strength of a negative photo-
actic response in walleye proved to be largely dependent on the given
respiratory situation: during 0£ depletion and during buildup of free
C02» the response diminished to the point of obliteration. This occurred
at levels of O2 which left mobility and equilibrium of the fish intact
(Scherer 1971).
135
-------
Table 3-12. Summary of lethal levels of dissolved oxygen for fishes occurring In the upper malnstem of the Ohio River and Allegheny and Monongahela Rivers.
Species of Fish
Scientific and
Common Name
CLUPEIDAE
Dorosoma cepedlanum
Clzzard shad
Age
or
Size
Dissolved
°?
HR/l
<1.0*
Deaths Exposure
Temp
°C
Most Declining 0^ 16
Reference
Hart (1945)
Remarks
*C(>2 tensions 25 mm Hg or less
HIODONTIDAE
Hlodon alosoldes
Goldeye
ESOCIDAE
Esox luclus
Northern pike
9.4 g
9.4 g
0.7-1.6*
1.2-1.5*
3.1
2.3
100Z
1003!
Declining O2
Constant Oj
24 hours*
Constant O2
48 hours*
15
15
4 or
less
Hart (1968) *Range of lethal levels for Individual fish; OOj
tensions 30 mm Hg or less
*Same as above
Moore (1942) *Flsh held In a cage submerged In a lake In summer
*Flsh held In a cage submerged In a lake In winter
0.2-0.5
0.3-0.6
1-2 yr 0.5-1.6
0.7-1.4*
Flngerllngs 1.0-6.0
100Z
First
Declining O2 0-20
About Declining 0. 15-25
50*
100Z at Constant O2
1.0 mg/1 24 hours
15-29
21.5
Prlvolnev and
Koroleva (1953)
Prlvolnev (1954) Methods unknown
Shkorbatov (1965) *Vater gradually replaced with low 0^ water; averages of
individual lethal levels reported
Prlvolnev (1964) *Reported threshold concentrations; methods unknown
Petit (1973) All fish survived at 1.5 to 5.0 DO levels. Fish showed
signs of stress at 1.5, 2.0, 3.0, and 4.0 mg/1 DO levels
as compared to control, 6.0 mg/1. Signs of stress:
Increased opercular movement, color bleaching, air gulp-
ing, resting on bottom, lack of feeding.
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Esox luclus
Age Dissolved
or On
Site mg/1
Fertilized 9.4
Northern pike egg to feed-
(cont.) lng larvae
4.9
2.6
1.3
4.9
Deaths Exposure
43.5Z
47.61
95.0*
1001
421
Constant 0
at 20 days
Juveniles
2.9
7.20
93.53:
0Z
Constant 0
Embryo
5.39
2.60
1.74
0.6
1.8
2.6
8.0
0Z
0Z
0Z
23Z
20Z
7*
17Z
Variable 0
8 hours
Remarks
Reference
Slefert et al. Significant mortality at DO levels below 4.9 mg/1
(1973)
Slefert et al. Significant mortality at 2.9 tng/1 DO
(1973)
Adelman and Smith Decreased growth at <4.0 mg/1 DO
(1970)
Peterka and Kent Hatching success comparable at all DO levels
(1976)
-------
Tabic 3-12. (continued)
Species of Fish
Scientific and
Common Name
Esox luclus
Northern pike
(cont.)
Age
or
Size
Sac larvae
Early feeding
larvae
CYPRINIDAE
Campostona anomalum
Stoneroller
Carasslus auratus
Goldfish
1 yr
6 g
6 g
Dissolved
°?
mg/1
0.3
2.0
4.8
10.1
0.5
1.6
4.0
8.9
0.90
1.4
<2.0
0.1
0.6
Deaths Exposure
49* Variable 0„
13*
9Z
82
1002
too*
02
72
100*
None
1002
1002
None
8 hours
Temp
°C
8-11
8-11
8-11
8-11
12-14
12-14
12-14
12-14
Declining 0^* 30
Declining 0j* 30
Declining 0j 1-32
Constant 0- 27-28
40 mln
Constant Oj 27-28
9 hours
Reference
Peterka and Kent
(1976)
Remarks
Survival significantly less at 0.3 mg/1 DO
Good survival above 4.0 mg/1 DO
Baker (1941) *Fish not allowed access to surface
*Flsh not allowed access to surface; test discontinued at
12 hours
Fry et al. (1947) COj tensions 0-100 mm Hg
Basu (1949)
-------
Table 3- 12. (continued)
Species of Fish
Scientific and
Common Name
Carasslus auratus
Goldfish (cont.)
Cyprlus carplo
Common carp
u
ID
Age
or
Slate
6 g
Dissolved
°?
PR/I
1.0
8 cm 0.4-0.8
8 cm 0.4-1.2
Deaths Exposure
50*
50Z
8 cm 2.8 SOX
0.2-0.3 First
2 yr 0.3-0.8*
0.5-79 g 0.2-0.7*
Temp
°C
None Constant O 21-27
24 hours
Constant O. 10-20
1 day
Constant O. 10-16
7 days
20
0
Declining 0^ 5-8
12-18
1.6-10 1.1-1.3
®g
245-658 0.6-0.7
mg
Embryo 0
50Z*
50Z*
21-22
19
100Z Constant 0^ 25
1.2
3.0
96X
60Z
25
25
Reference
Basu (1949)
Remarks
Downing and
Merkens (1957)
Prlvolnev (1954) Methods unknown
Streltsova (1964) 'Lethal Oj level varied with acclimation to various O2
levels
Opuszynskl (1967) *Range of Individual lethal levels; cessation of
respiratory movement
Kumetsova (1958) *Loss of balance with cessation of respiratory movement
(ambiguous)
*Same as above
Kaur and Toor Percentage hatching Increased with increasing DO content
(1978) Eggs maintained at low DO developed more slowly; time to
hatching increased as the DO level decreased. No abnor-
malities In hatched embryo observed.
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Cyprlnus carplo
Commonn carp
(cont.)
Age
or
Size
Dissolved
0,
mg/l
Notemlgonus crysoleucas
Golden shiner
Embryo - 6.0
9.0
12.0
1.4
Notropls cornutus
Common shiner
1-2 yr
1-2 yr
1-2 yr
<1.0*
1.4-6.2
0.5-1.0
0.4-0.6
27.5 g <2.0*
Deaths
352
82
22
None
Most
First*
50**
10031*
100Z
Exposure
Constant O.
Constant 0
48 hours* ^
Declining Oj
Temp
°C
25
25
25
4 or
less
15-16
12-27
12-27
12-27
17-22
Notropl3 whlpplel 5 cm 1.0 502*
Steelcolor shiner
Plmephales notatus 4 cm 0.8-1.3 502*
Bluntnose minnow
Plmephales promelas 3.9 g <2.0* 1001
Fathead minnow
20-26
7-24
18-21
Reference
Remarks
Kaur and Toor
(1978)
Moore (1942) *Fish held in a cage submerged in a lake in winter
Hart (1945) *C02 tensions 60 mm Hg or less
Cooper (1960) *Loss of equilibrium
Black et al.
(1954)
Wilding (1939)
*Loss of equilibrium
*Loss of equilibrium
*C02 tensions 0-40 mm Hg
*Loss of equilibrium; values obtained by interpolate
from graph
*Same as above
Black et al.
(1954)
*C02 tensions 0-40 mm Hg
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Plmephales promelas
Fathead minnow
(cont.)
Age Dissolved
or On
Site hr/1 Deaths Exposure
3.6 cm 1.0
None*
Constant 0^
IB hourG
Temp
*C Reference
18-26 Uhltworth and
Irwin (I960
Reproduction 1.00-7.92
Constant 0
15-25 Brungs (1971)
Fry survival 2.02-7.26
and growth
Scmotllus atromaculatus 2-3 yr <2.0*
Creek chub
CAT0ST0MIDAE
Catostomus commersonl 265 g <2.0*
Uhlte sucker
Fertilization 7
to hatching
6
5
3
Embryo to 1.2
feeding larvae
100X
100Z
81.7%
80.IX
73.7X
71.5-
75.BX
100X
Declining 0 17-21
Declining 0_ 17-18
Constant
Constant Oj
mortality at
22 days
Black et al.
(1954)
Black et al.
(1954)
Oseld and Smith
(1971)
12.3
12.9
12.3
12.3
& 12.9
IB Selfert and Spoor
(1974)
Remarks
*Also In tests with declining CO2
No effect on egg production for fish reared at DO concen-
trations of 3.00 to 7.92 mg/1. Eggs per female lower at
2.0 mg/1, and no eggs were laid at 1.0 mg/1.
Fry survival was reduced at <4.0 mg/1; 18X survivors at
4.0 mg/1 were deformed. Fry growth was reduced at all DO
concentrations below the control (7.26 mg/l).
~COj tensions 0-40 ram llg
•COj tensions 0-40 mm llg
Days to 95X hatch—14; mean length at hatching—10.1 mm
Days to 95X hatch—11; mean length at hatching—8.9 mm
Days to 95X hatch—14; mean length at hatching—10.1 mm
Days to 95X hatch—13 to 14; mean length at hatching —
8.3-9.7 mm
No harm apparent at 4.5 mg/1. Good hatching at 2.5 mg/1,
but growth suppressed. Time to first feeding comparable
among control and larvae reared at 4.9 mg/1 but extended
for larvae reared at 2.5 mg/1.
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Catostomus commersonl
White sucker
(cont.)
ICTALURIDAE
Ictalurus catus
White catfish
Ictalurus melas
Black bullhead
Age
or
Size
Brovm bullhead
Dissolved
°2
mg/1 Deaths
2.5
4.9
9.1
<1.0*
3.0
0.3
Ictalurus nebulosus 36 g <1.0*
<1.0
Ictalurus punctatus Juvenile 1.0-1.1*
Channel catfish
2.0*
10.5Z
4.5*
8.0Z
100*
100?
100*
100Z
Most
Exposure
Constant O2
mortality at
22 days
Constant O2
24 hours
Temp
°C
18
18
18
Declining Oj 12-16
Constant O2* 22
24 hours
Constant 02* 4 or
48 hours less
Declining Oj 19-22
12-16
25-35
30
0.8-0.9* —
Gradually
declining Oj>
reduced dally
25-35
Reference
Selfert and Spoor
(1974)
Remarks
Hart (1945)
*C02 tensions 100 ram Hg or less
Moore (1942) *Fish held in a cage submerged in a lake in summer
*Fish held in a cage submerged in a lake in winter
Black et al.
(1954)
Hart (1945)
Moss and Scott
(1961)
*C02 tensions 0-40 ram Hg
*C02 tensions 100 mm Hg or less
^Estimated average tolerance limits for "normal" fish
*Estlmated average tolerance limits for "excessively fat,
overfed fish
~Estimated average 24-hr tolerance limits
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Age
or
Size
Dissolved
or! 1
Deaths Exposure
Temp
*C
Ictalurus punctatus Juvenile 7.7-2.0 01
Channel catfish
(cont.)
6.0-8.0 0?
to 0.4-3.9
Fingerllng 3.0-6.8 OX
growth
Constant 0,
69 days
25
Dlel fluctua- 25
ting Oj 69 days
Constant Oj
177 days
27
8.3
5.0
3.0
8.3
5.0
3.0
Embryo to 7.8
first feeding
5.8
5.0
4.2
2.4
Embryo to 7.3
first feeding
OZ
OX
33.51
36. OX
44.52
62.5*
92.51
33.0*
Constant
for 14 weeks
.5,
ration fixed
Constant 0£
for 6 weeks,
fed ad libitum
Constant 0,
19 days
26.6
26.6
25
25
25
25
25
28
Reference
Remarks
Carlson et al. Growth less at 2.0 and 3.5 mg/1 DO, comparable at 5.0,
(1980) 6.5, and control. Fish at 2.0 mg/1 stressed.
Ralble (1975)
Andrews et al.
(1973)
Growth less than In constant DO test. Only fish reared
at lowest DO showed less growth than control.
Fish died at DO levels <1.0 mg/1. Weight gain ranged
from 706 to 12I0X and was highest at 6.0 mg/1 and lowest
at 3.0 mg/1.
Growth at 3.0 mg/I ¦ 1/2 that at >5.0 mg/1. Fish at 3.0
mg/1 leas active.
Poor growth In fish at 3.0 mg/1, moderate growth at 5.0
ng/1, best growth at 8.3 mg/1.
Carlaon et al. Survival significantly less at 2.4 and 4.2 mg/1; growth
(197
) reduced, hatching and first feeding delayed at all DO
levels below 7.8 mg/1.
Survival significantly less at 2.3
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
letalurus punctatus
Channel catfish
(cont.)
Age
or
Size
CYPRINODONTIDAE
Fundulus dlaphanus
Banded kllllfish
GASTEROSTEIDAE
Culea lnconstans
Brook stickleback
PERCICHTHYIDAE
Horone chrysop3
White bass
Fertlllia-
tlon to
hatching
CENTRARCHIDAE
Ambloplltes rupestrls —
Rock bass
Dissolved
°2
PR/1
5.4
4.6
3.8
2.3
0.9
0.6 g <2.0*
Lepoats Rulosus
Warmouth
13 co
9.2
6.9
5.0
3.4
1.8
2.3
0.4-J.6
Deaths Exposure
46.OX
48. OX
47.0Z
1002
100Z
100Z
60.5*
53.1Z
61.0Z
5B.8Z
57.0Z
100Z
100Z
Constant O.
19 days
Constant O2
mortality at
hatch
Constant Oj*
48 hours
Temp
°C
28
28
28
28
Constant Oj* 4 or
less
Declining Oj 20-23
16
16
16
16
16
4 or
less
Declining Oj* 21-32
Reference
Carlson et al.
(1974)
Remarks
Moore (1942) *Flsh held In 8 cage submerged In a lake In winter
Black et al.
(1954)
*C02 tensions 0-40 mm Hg
Slefert et al. No trend In survival at hatch with regard to decreasing
(1974) DO. Larval survival at 7 days post-hatch lower at 1.8
mg/1 DO.
Moore (1942) *Pish held In a cage submerged In a lake In winter
Baker (1941) *Plsh not allowed access to surface
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Lepomls gulosus
Uarmouth
(cont.)
Lepomls cyanellus
Green sunflsh
Lepomls glbbosus
Pumpklnseed
Lepomls hum!lis
Orangespotted
sunflBh
Age Dissolved
or 0?
Size uk/1 Deaths Exposure
13 cm 0.7-1.3
1.5
3.1
0.9
24 g <2.0*
7.6 g 0.9-1.1
7.6 g 0.2
1.4
Lepomls macrochlrus 2-6 cm 0.6-1.1
Bluegl11
2-7 cm 0.5-1.0
Temp
°C Reference
None
100Z
100Z
100Z
None
100Z
100Z
None
Declining C^* 21-32 Baker (1941)
Constant 0^
48 hours*
100J Constant Oj
24 hours*
Constant 0.
48 hours*
4 or
less
15
4 or
less
Hoore (1942)
Remarks
*Fl8h allowed access to surface; tests discontinued at 6
to 20 hours
*Flsh held In a cage submerged In a lake In vlnter
*Flsh held In a cage submerged In a lake In summer
*Flsh held In a cage submerged In a lake In winter
100X Declining 0
19-21 Black et al.
(1954)
*C0j tensions 0-40 mm Hg
Declining Qj* 25-28 Baker (1941) *Flsh not allowed access to surface
22-23
4 or Hoore (1942)
less
Constant 0.
48 hours*
Declining 0?* 24-30 Baker (1941)
24-29
*Flsh allowed access to surface; test discontinued at 24
hours
*Flsh held In a cage submerged In a lake In winter
*Flsh not allowed access to surface
*Flsh allowed access to surface; test discontinued at 12
to 24 hours
5 cm 0.9
50Z
30
*Flsh allowed access to surface
-------
Table 3-12.
(continued)
Species of Fish
Scientific and
Common Nane
Lepomls macrochlrus
Blucgl11
(cone.)
Age
or
Sire
Dissolved
02
mg/1
Juvenile 0.5
6-20 g
6-20 g
Embryo
0.8-1.2*
0.7-0.9*
3.1
0.8
<1 .0*
0.5
2.1
3.0
7.8
Sac larvae 0.5
1.8
3.7
8.0
Deaths
100*
1007.
1007.
Most
60%
54%
502
53%
997.
30%
35%
31%
Exposure
Declining 0^
Constant O2
24 hours
Gradually
declining 0-,
reduced dally
Constant
24 hours*
Constant
48 hours*
Declining 0^
Variable Oj
4 hours
Temp
°C
20
25-35
25-35
15
4 or
less
15-16
25-28
25-28
25-28
25-28
21-26
21-26
21-26
21-26
Reference
Remarks
McNeil (1956)
Moss and Scott
(1961)
~Estimated average tolerance limits
~Estimated average 24 hour tolerance limits
Moore (1942) *Flsh held in a cage submerged In a lake In summer
*Fish held In a cage submerged In a lake in vrinter
Hart (1945) *C02 tensions 25 mm Hg
Peterka and Kent Survival comparable at all DO levels
(1976)
Survival comparable at DO levels >1.8 mg/1
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Bluegl11
(cont.)
Age
or
Size
Dissolved
°2
mR/1
Flngerllng9 0.8-6.0
Lcpomls mlcrolophns
Redear sunflsh
24 g
« S
<1.0*
Mlcropterus dolomleul 255 g <2.0*
Sraallmouth bass
0.9-1.6
Deaths Exposure
100Z
at 0.8
rag/1
100?
100*
First*
Constant 0^
24 hours
Temp
"C
21
Declining 0, 20-21
15-25
11-27
4 g
4 g
0.6-1.2
0.5-1.0
Fertilized 8.7
egg to feed-
ing larvae
507.*
1007.
50.0Z
Constant
mortality at
14 days
11-27
11-27
20
4.4
2.5
1.2
4.4
63.5X
100*
100X
70*
20
20
20
25
2.2
100Z
25
Embryo 0.5
100*
Variable 0. 20-23
2
6 hours
Reference
Remarks
Petit (1973) All survived at 1.0 to 5.0 mg/1 levels. Fish stressed at
DO levels from 1.0 to 3.0 mg/1.
Black et al. *C02 tensions 0-40 mm Hg
(1954)
*COj tensions 0-40 mm Hg
Burdlck et al. *Loss of equilibrium
(1954)
*Loss of equilibrium
*Loss of equilibrium
Slefert et al. Successful hatching at all DO levels; total mortality of
(1974) larvae before 14 days at lowest DO levels. At 4.4 mg/1,
rate of development approximated control but larval size
smaller than control.
Development more rapid than at 20°C, growth was greater,
and feeding started earlier.
Peterka and Kent Mean hatching success comparable at DOs >1.8.
(1976)
-------
Table 3-12. (continued)
Species of Fish Age Dissolved
Scientific and or On Temp
Common Name Size mg/1 Deaths Exposure "C
Mlcropterus dolomieul Embryo
Snallmouth bass
(cont.)
1.8
3.5
3U
13*
Variable 0-,
6 hours
20-23
20-23
-
7.9
9X
••
20-23
Sac larva
0.5
1001
Variable 0,
6 hours
17
-
2.2
472
17
••
4.2
27*
••
17
9.0
17X
-
17
Mlcropterus 9almoldes 4-14 g
Largemouth bass
0.9-1.4*
—
Constant Oj
24 hours
25-35
4-14 g
0.8-1.2*
Gradually
declining 02>
reduced daliv
25-35
--
3.1
100X
Constant 0j
24 hours*
15
—
2.3
100*
Constant 02
48 hours*
4 or
less
—
<1.0*
100*
Declining 0^*
12-16
Flngerling
1.0-6.0
loo*
at 1.0
Constant
24 hours
25
rag/I 02
Reference
Remarks
Peterka and Kent
(1976)
Mean hatching success comparable at DOs >2.2 mg/l
Mos9 and Scott 'Estimated average tolerance limits
(1961)
~Estimated average 24-hour tolerance limits
Moore (1942) *Fish held in a cage submerged in a lake in summer
*Fish held In a cage submerged in a lake In winter
Hart (1945) *C02 tensions 50 mm Hg or less
Petit (1973)
All survived at 1.5 to 5.0 mg/l levels. Fish stressed
DO levels from 1.5 to 5.0.
-------
Table 3-12. (continued)
Specie? of Fish
Scientific and
Common Name
Age
or
Size
Dissolved
°2
°>K/1
Hlcropterus aalmoldes
L.irgeraouth Fertilized 8.6
bass (cont.) egg to feed-
ing larvae
6.3
Deaths Exposure
10.9X
11.82
Constant
20 days
Terap
"C
20
20
4.5
11.81
20
3.1
24 .61
20
1.7
99.6X
20
Embryo
8.3
6.0
4.2
3.0
1.7
2.0
25.5* 23
10.9* 23
38.2* " 23
22.8* 23
100* " 23
Too Hatching 15
2.1
2.8
20
25
Reference
Remarks
Carlson and Control in these experiments; hatching nnd feeding began
Slefert (1984) at hours 50 nnd 193, respectively.
Hatching and feeding began at hours 56 and 195, respec-
tively
Hatching and feeding began at hours 49 and 204, respec-
tively
Hatching and feeding began at hours 51 and 216, respec-
tively
Hatching and feeding began at hours 47 and 220, respec-
tively
Control in these experiments; initial feeding at 124 hours
Initial feeding at 124 hours
Initial feeding at 129 hours
Initial feeding at 170 hours
None fed
Dudley and Elpper Embryo mortality occurred tor these DO levels and terapera-
(1975) tures (2.0 to 2.8 rag/1; 15 to 25"C)
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Age
or
Size
Mlcropterus salmoldes Embryo
Largemouth bass and
(cont.) larval
Dissolved
¦"K/l
2.0
Deaths Exposure
Temp
•c
Too Hatching 15
Pomoxls annularis
White crappie
23 cm
23 cm
Pomoxls nlgromaculatus —
Black crappie
Adult spawning,
embryo, larvae
2.5
3.5
0.4-0.5
0.4
4.3
1.4
1.0*
5 levels,
2.5 to air
saturation
100Z
50*
lOOt
100*
Most
20
25
Declining 0^* 27
Declining 0^* 27
Constant O
24 hours*
Constant 0.
48 hours*
Declining
Constant 0„
26
4 or
less
16
20
5 levels, — " Varying
2.6 to air 15-21
saturation
4 levels — Diurnally
fluctuating
°2
Reference
Remarks
Dudley and Elpper These DO levels produced the same percentage of normally
(1975)
shaped larvae that water at 903! oxygen saturation (I.e.,
15°C and 9.13 mg/l, 20°C and 8.25 mg/1, 25°C and 7.54
mg/1) produced
Baker (1941)
*Flsh not allowed access to surface
Baker (1941) *Flsh allowed access to surface
Moore (1942) *Flsh held in a cage submerged in a lake In summer
Moore (1942)
*Flsh held in a cage submerged In a lake in winter
Hart (1945)
Slefert and
Herman (1977)
Carlson and
Herman (1978)
*C0£ tensions 30 mm Hg or less
Reduce DO concentrations over the range tested had little
or no effect on the occurrence of successful spawning or
on the number of embryos, viability, hatching success, and
survival through swlm-up stage
Successful spawning occurred in all treatments
Successful spawning did not occur in lowest fluctuating
treatment <1.8 to 4.1 mg/1)
-------
Table 3-12.
(continued)
Species of Fish
Scientific and
Common Name
PERCIDAE
Perca flavescens
Yellow perch
Age Dissolved
or Q, Temp
Size in g/l Deaths Exposure *C
78 g <2.0*
89-99 g 0.5-0.8
100Z Declining 02 19-24
50** Declining 02 12-21
3.1
1.5
7.6 era 0.9-1.1
I00Z Constant 0^ 15
24 hours*
100Z Constant O2 4 or
48 hours* less
50X* Declining 02 18-27
Flngerllngs 1.0-6.0
Juvenile
Stlzostedlon vltreura
Wal1 eye
1.0-6.0
8.5-2.0
6.8-9.1 to
0.7-5.0
1.4-6.0
Flngerllngs
100Z
at 1.0
rag/1
0
0
Constant 0^
24 hours
Constant Oj
67 days
22.8
15.2
20
Dlel fluctua- 20
ting O.
67 days
100Z
at 2.0
Constant Oj
24 hourB
22.8
Reference
Remarks
Black et al.
(1954)
Burdlck et al.
(1957)
Moore (1942)
*COj tensions 0-40 mm fig
*Loss of equilibrium
*Flsh held In a cage submerged in a lake in summer
Moore (1942) *Flsh held In a cage submerged In a lake In winter
Wilding (1939) *Loss of equilibrium; values obtained by Interpolation
from graph
Petit (1973) All fish survived at DO levels of >1.5 mg/1. Stress
apparent at <4.0 og/1.
100Z survival at 1.0 rag/1
Carlson et al. Crowth poor at 2.0 rag/1, comparable at 8.5, 6.5, 5.0, and
(1980) 3.5 rag/l.
Crowth comparable at nil DO levels
Petit (1973) Pish died at 2.0 and 1.4 mg/1 DO, but none died at levels
of >3.0 mg/1.
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Age
or
Size
Dissolved
°?
mg/1
Deaths Exposure
Temp
"C
Stlzostedlon vltreum Egg to
Walleye hatching
(cont.)
2-6
42 to
697.
survival
to hatching
Constant 0-
12.4-
cXI
rvo
Embryo to 1.3 1002 Constant O2 17
feeding mortality at
larvae 20 days
2.0 100Z " 17
2.4 100* " 17
3.4 85.5Z " 17
4.8 61.5X " 17
8.9 58.5 " 17
2.3 100X Constant 20
mortality at
20 days
4.5 99.5X " 20
8.4 98.OX " 20
Reference
Remarks
Oseld and Smith
(1971)
Time to hatching was extended, survival was diminished,
and mean length was reduced when DO was decreased from 6.0
to 3.0 mg/1.
Slefert and Spoor Survival In control (8.9 mg/1 DO) and at 50? saturation
(1974) (4.8) comparable; at 3551 saturation (3.4 mg/1 DO) and
below survival markedly reduced. Larval size at hatching
comparable In control and 505! saturation; at saturations
of <352, size at hatching reduced. Start of feeding
comparable In control and at 50Z saturation.
Development faster than at 17°C, but few survivors.
-------
Table 3-12. (continued)
Species of Fish
Scientific and
Common Name
Age
or
Size
Dissolved
°?
rag/1
Deaths
Exposure
Temp
*C
Reference
Remarks
SCIAENIDAE
Aplodlnotus grunniens
Freshwater drum
—
4.3
loot
Constant 02
26 hours*
26
Moore (1942)
*Fish held In a cage submerged In a lake In summer
aThe (symbol < preceding an Oj concentration value In this column Indicates that several or numerous lethal O2 concentrations reported were all less
than (often nr.ich less than) the value shown.
b"Decllnlng O2" signifies gradual reduction of 02; unless otherwise noted under Remarks, 02 "as reduced by respiration of test fish.
cReferences cited dated from 1937 to 1970 inclusive taken from Doudoroff and Shuraway 1970. References subsequent to 1970 are Included In Literature
Cited.
co
dThe nsterlsk (*) 1s used to indicate to which item or items in the columns at the left the remark pertains or Is most pertinent.
-------
Some species show an ability to acclimate to lowered ambient oxygen.
However, the advantage gained is not clear. Acclimation can enhance blood
oxygen capacity and oxygen utilization somewhat but may not aid active
swimming performance. Acclimation may be useful to fish subjected to
gradual reductions in oxygen levels, but would be of little advantage to a
fish encountering rapid and severe reductions (Davis 1975). Acclimation by
study area species may be accommodated by reduction in movements,
increasing hematocrit levels, or alteration of heart rate, all adaptations
observed in freshwater fishes (Hoss and Peters 1976).
Migration into lower reaches of tributaries is another mechanism by
which fish in the study area would be able to escape anoxic or hypoxic
conditions. Krumholz and Minckley (1964) suggested that tributaries often
provided a refugia for species typically occurring in the upper mainstera of
the Ohio River. Gammon and Reidy (1981) observed that a variety of Wabash
River fishes concentrated in the mouths of tributaries during an episode of
low dissolved oxygen during July and August 1977.
The above information characterizes the responses of and adaptations
by fishes to low dissolved oxygen concentrations. The remaining portion of
this review is concerned with levels of oxygen that actually result in
mortality (Table 3-12). The primary source of information for this summary
was Table 1 in Doudoroff and Shumway (1970); information for species
occurring in the study area was abstracted from this table and is included
herein. Additionally, studies published subsequent to Doudoroff and
Shuraway's compendium have been added. Habitat suitability information
compiled by the U.S. Department of the Interior for several study area
species was reviewed, but no data regarding dissolved oxygen requirements
for any life stage was available. Species accounts reviewed for which O2
data were lacking included: blacknose dace (Trail et al. 1983), black
bullhead (Stuber 1982), smallraouth buffalo (Edwards and Tworaey 1982),
bigmouth buffalo (Edwards 1983), creek chub (McMahon 1982), common shiner
(Trail et al. 1983), and green sunfish (Stuber et al. 1982). No
information on dissolved oxygen tolerance was available for the majority of
species in the study area.
154
-------
The levels of dissolved oxygen shown to be lethal to fish are gener-
ally below 4.0 mg/1 (Table 3-12). Species that could tolerate dissolved
oxygen levels below 3.0 mg/1, with some individuals surviving, including
gizzard shad, goldeye, northern pike, stoneroller, goldfish, carp, golden
shiner, common shiner, steelcolor shiner, bluntnose minnow, fathead minnow,
creek chub, white sucker, white catfish, black bullhead, brown bullhead,
channel catfish, banded killifish, brook stickleback, white bass, rock
bass, warmouth, green sunfish, pumpkinseed, orangespotted sunfish, blue-
gill, redear sunfish, smallmouth bass, largeraouth bass, white crappie,
yellow perch, and walleye. Among these species are several that numeric-
ally dominate the fish community of the study area rivers, contribute
substantially to the biomass, or are important to the sport catch. Gener-
ally, when the same species was tested at high and low temperatures, it had
a greater tolerance for low dissolved oxygen levels at low rather than at
high water temperatures. Two species that would undergo stress at 4.0 mg/1
at summer temperatures are the black crappie and the freshwater drum.
Tolerance of embryonic and larval stages to low dissolved oxygen
concentrations for select species was evaluated and survivorship at
dissolved oxygen levels above 3.0 mg/1 was generally good. Low dissolved
oxygen levels and high temperatures in study area rivers typically occur
late during summer. Most species occurring in the study area are spring
and early summer spawners, therefore, low dissolved oxygen levels resulting
from hydroelectric facility operations should not affect embryological
development or hatching success. Larval stages and fingerlings, as well as
juveniles and adults, would be affected by low dissolved oxygen levels
should they occur.
3.7 IMPACTS OF HYDROPOWER PLANT OPERATION ON INDIGENOUS FISH SPECIES
Bell et al. (1967, 1981) provided a comprehensive review of the
success of passage of small fish through hydroelectric power generating
turbines. His review centered on the anadromous salmonid fisheries of the
Columbia River in the Pacific Northwest, but included Canadian and European
studies as well. Each location evaluated had either a Francis or Kaplan
turbine. Fish losses were attributed to mechanical injuries—abrasions,
155
-------
contusions, or lacerations; pressure injuries—popped eyes and gill
hemorrhages; or shearing action injuries—torn opercula and broken gill
arches (Bell et al. 1967, 1981; Turbak et al. 1981). Based upon extensive
regression analyses of Francis and Kaplan turbine operational and fish loss
data, Bell et al. (1967) concluded that successful passage of fish through
turbines was most related to total machine operating efficiency, which is
related to wicket gate opening, quantity of water at the head used, and
blade angle setting. Generally, highest survival was observed at the point
of highest total efficiency for both turbine types. Reported percent
survival of fish tested ranged from 0 to 100 percent, but average percent
survival was 75 percent in 20 of 32 tests conducted (Bell et al. 1967).
Olson and Kaczynski (1980) reported the results of survival evalua-
tions of downstream migrant coho salmon and steelhead trout through
horizontal-axis bulb turbines at Rock Island Dam on the mid-Columbia River.
The estimated survival rate for yearling coho salmon smolts passing through
the bulb turbine was 93 percent (95 percent confidence intervals equals
90.4 to 95.6 percent); steelhead smolt survival was estimated at 96.9
percent (95 percent confidence interval of 88.0 to 105.9 percent).
The effect of hydropower development on anadromous fishes of the
northeast United States was reported by the U.S. Fish and Wildlife Serivce
in 1982. In that publication, Kynard et al. discussed the effects of
Kaplan turbines on Atlantic salmon smolts, American shad, and blueback
herring; Gloss et al. discussed the effects of Ossberger turbines on
Atlantic salmon smolts, striped bass, and American shad; and Knight and
Kuzmeskus described the potential effects of bulb turbines on Atlantic
salmon smolts. The latter study was conducted at Essex Dam along the
Merrimack River at Lawrence, Massachusetts. Knight and Kuzmeskus reported
98 percent survival of salmon smolt five hours after plant passage.
The preceding studies reveal that few bulb turbine equipped hydroplant
fish mortality studies have been conducted. Those completed have dealt
with anadromous, cold water fisheries in coastal areas. A field study that
will document fish survival at a bulb turbine equipped hydroplant located
along a warm-water, midwestern river remains to be conducted.
156
-------
4.0 DISCUSSION
4.1 EVALUATION OF WATER QUALITY MODEL PREDICTIONS
The modeling analyses included the development of the calibrated
model, the verification of the model accuracy under another set of condi-
tions, sensitivity analyses for key parameters, and analysis of various
hydropower development scenarios. Based on the calibration and verifica-
tion results, a high level of confidence in the model accuracy is indi-
cated. The available data were sufficiently detailed to provide a level of
resolution suitable for the purpose of the study. The dissolved oxygen
profile predictions compare very well to the shape of the observed data
profiles, and except for the inability of the model to completely demon-
strate the supersaturated condition on the Ohio River, the dissolved oxygen
levels show good agreement.
The sensitivity analyses indicated that the model is fairly insensi-
tive to small changes in the parameter values selected. The greatest
sensitivity appears to be with the light extinction coefficient effect on
algal populations and consequent impacts on dissolved oxygen levels.
The results of the hydropower development scenarios indicated there
would be a cumulative impact on dissolved oxygen levels at the LTMA flow
rate, but that this impact would not be of sufficient magnitude to cause
water quality violations (depression of dissolved oxygen levels below 5.0
mg/1) in the study area. The extreme case of no reaeration at the locks
and dams (i.e., 100 percent flow through the turbines with no reaeration
from the dam) indicated reduced dissolved oxygen levels just downstream of
each dam, but these predicted levels are well above the stream standard of
5.0 mg/1. The results from the 50 percent flow condition show reduced
impacts from hydropower development. Based on the planned hydropower
development announced for these locks and dams, the flow through the
turbines would never be 100 percent, and would most likely be around 80
percent at the LTMA condition. J Therefore, it is expected that the cumula-
tive dissolved oxygen deficit within the study area from complete hydro-
157
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power development would fall somewhere between the 50 percent and 100
percent scenarios.
The results from the LFE analysis are similar to the results from the
LTMA. There is a stronger indication of a dissolved oxygen deficit at the
lower reaches of the Ohio River, but no water quality violation is
predicted to occur within the study area.
The down river impact of hydropower development (i.e., below Ohio
River Mile 40) was not included in the scope of this study. There would be
concern in these lower reaches, based on the trend of the dissolved oxygen
levels predicted in this study and the indication that the deficits will be
cumulative. There also have been a higher number of dissolved oxygen water
quality criteria violations in the lower Ohio River reaches (0RSANC0 1980,
1982, 1984), which could be exacerbated by hydropower development. If this
were the situation, then the slightly reduced dissolved oxygen levels at
the lower study boundary (Ohio River Mile 40) could be significant.
A limitation in evaluating these results is the condition upstream of
the study area. The large number of potential development sites on the
upper Allegheny and upper Monongahela Rivers could change the upstream
conditions as used in this study (i.e., the headwater conditions). An
investigation of these upper reaches for cumulative impacts of hydropower
development could result in a lower dissolved oxygen predicted as a head-
water condition for this study. This would then affect the predictions for
the Allegheny and Monongahela Rivers.
4.2 EVALUATION OF BIOLOGICAL IMPACTS ASSOCIATED WITH LOW DISSOLVED OXYGEN
VALUES
The upper Ohio River and Allegheny and Monongahela Rivers have a fish
community composed of 122 species distributed among 20 families. Biologi-
cal monitoring has been conducted in the study area during the past 30
years, resulting in a fairly detailed characterization of the fish fauna
for recent times. Following the categorization of fishes provided by
Preston and White (1978), the fish fauna of the study area is dominated,
either numerically or in biomass, by species in the following categories:
158
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Category
Species Included
Forage A
Emerald shiner, bigeye shiner, ghost shiner,
striped shiner, rosyface shiner, spotfin
shiner, sand shiner, mimic shiner, and blunt-
nose minnow
Forage B
Sport A
Gizzard shad
White bass, rock bass, green sunfish,
pumpkinseed, warmouth, bluegill, smallmouth
bass, largemouth bass, spotted bass, and
white crappie
Sport B
Yellow perch and walleye
Commercial
White catfish, channel catfish, flathead
catfish, quillback, and freshwater drum
Rough
Longnose gar, carp, goldfish, white sucker,
northern hogsucker, golden redhorse, black
bullhead, yellow bullhead, and brown
bullhead
Miscellaneous
Trout-perch, Johnny darter, and logperch
Many other species typically accompanied the above dominants in fish
collections, however, the others occurred at low density, typically have
low bioraass, but added richness to the community.
The study area provides seven different habitats for spawning, (I) the
main channel, (2) main channel border, (3) the shore-debris zone, (4) tail
waters, (5) side channels, (6) sloughs and embayments, and (7) creek mouths
and - flooded channels. Some or all of these areas are used as spawning
sites, for larvae and juveniles of 13 of the 20 families occurring in the
study area have been collected in ichthyoplankton tows or in entrainment
samples, 59 taxa in all.
159
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Spawning occurs primarily during spring and early summer. Thus, most
species and the peak period(s) of ichthyoplankton density preceed adverse
conditions that could be associated with the late summer high temperature-
low river flow period. With locks and dams in the study area being
retrofit for hydropower production, the potential exists for dissolved
oxygen levels to be depressed during the late summer high temperature-low
flow condition. However, model predictions suggest that oxygen values will
remain high, average >5.0 mg/1 per day, therefore, no sustained impact to
the study area fishery is anticipated as a result of low dissolved oxygen
values. Tolerance of fishes to low dissolved oxygen levels suggest that
only minor impacts would occur so long as dissolved oxygen values remained
above 4.0 mg/1.
160
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5.0 CONCLUSIONS
The conversion of the locks and dams to hydropower will reduce the
reaeration in the study area. The complete removal of this reaeration will
be demonstrated as a reduction in dissolved oxygen levels in the study
area. The total reduction at the downriver location in this study area is
predicted to be about 1.4 mg/1 (at complete removal of reaeration) for the
lowest expected monthly average flow (LTMA). The reduction in dissolved
oxygen for the lowest flow expected (LFE) is also predicted to be about 1.4
mg/1.
The reduction in dissolved oxygen levels appears to be cumulative, and
appears to be more significant at the downriver reaches than at the upriver
locations. It appears that the natural reaeration at the upriver locations
compensates for the loss of reaeration at the upper locks and dams, but
that this natural reaeration is less adequate downriver.
The complete conversion of the locks and dams in the study area is not
predicted to create a water quality violation for dissolved oxygen. The
complete conversion could cause a violation downriver. However, this was
not evaluated in this study.
Under the conditions evaluated, dissolved oxygen values will remain
above 5.0 mg/1 and should be sufficient to protect aquatic life.
161
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6.0 RECOMMENDATIONS
The evaluation of hydropower impacts on dissolved oxygen should be
continued. It should include upriver evaluations on the Allegheny and
Monongahela Rivers to determine if a degraded water quality condition is
expected at the headwaters for this study. The study should be extended
downriver to determine if the cumulative dissolved oxygen deficit observed
in this study continues to be demonstrated.
The evaluation of each hydropower conversion proposal on the study
area rivers should include an evaluation of the existing lock and dam
reaeration. The result of the investigation should be compared to the
conditions in this study and evaluated to determine the potential impact on
these conclusions. In particular, the reaeration of the turbine tailrace
should be estimated. The reaeration of the turbine flow should be
evaluated as a mitigation requirement.
162
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